Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming, Water Years 2011 and 2012

Prepared in cooperation with the Jackson Hole Airport Board

Scientific Investigations Report 2013–5184

U.S. Department of the Interior U.S. Geological Survey

Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming, Water Years 2011 and 2012

By Peter R. Wright

Prepared in cooperation with the Jackson Hole Airport Board

Scientific Investigations Report 2013–5184

U.S. Department of the Interior U.S. Geological Survey U.S. Department of the Interior SALLY JEWELL, Secretary U.S. Geological Survey Suzette M. Kimball, Acting Director

U.S. Geological Survey, Reston, Virginia: 2013

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Suggested citation: Wright, P.R., 2013, Hydrogeology and water quality in the Snake River alluvial aquifer at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012: U.S. Geological Survey Scientific Investigations Report 2013–5184, 56 p., http://dx.doi.org/10.3133/sir20135184.

ISBN 978-1-4113-3717-6 iii

Acknowledgments

The author gratefully acknowledges the Teton Conservation District which maintains continuous groundwater level recorders at the Jackson Hole Airport and provided near real-time groundwater-level data for this study. The author gratefully acknowledges the assistance of Dan Leemon, Teton Conservation District, and the maintenance staff at the Jackson Hole Airport.

Steve Corsi and James Landmeyer, U.S. Geological Survey, are acknowledged for their technical reviews of report drafts. Janet Carter, U.S. Geological Survey, is thanked for report specialist review of this report. Scott Edmiston, Jerrod Wheeler, and Michael Sweat, U.S. Geological Survey, are thanked for their assistance collecting all of the data that made production of this report possible. iv

Contents

Acknowledgments...... iii Abstract...... 1 Introduction...... 2 Purpose and Scope...... 2 Description of Study Area...... 3 Study Design...... 3 Methods of Data Collection and Analysis...... 6 Well Construction and Ancillary Information...... 6 Water-Level Measurement...... 8 Water-Table Contours, Hydraulic Gradient, and Groundwater Velocity...... 8 Groundwater and Surface-Water Sampling and Analysis...... 8 Quality-Control Sample Collection and Data Analysis...... 11 Hydrogeology...... 14 Water Quality...... 23 Chemical Composition...... 23 Redox Conditions...... 23 Anthropogenic Compounds...... 28 Implications for Reduced Groundwater Conditions...... 31 Summary...... 31 References Cited...... 32 Appendixes...... 37

Figures

1. Map showing location of Jackson Hole Airport in the Jackson Hole valley, Wyoming...... 4 2. Map showing location of wells used in the study area for data collection, Jackson Hole Airport, Jackson, Wyoming...... 5 3. Map showing generalized geology and geologic section in the vicinity of the Jackson Hole Airport, Jackson, Wyoming...... 16 4. Graph showing water levels for selected wells sampled at the Jackson Hole Airport, Jackson, Wyoming with precipitation data collected at Moose, Wyoming, station 486428, water years 2008–12...... 19 5. Maps showing water-table contours and estimated direction of groundwater flow in low water table in April 2012 and high water table in July 2012, Jackson Hole Airport, Jackson, Wyoming...... 20 6. Trilinear diagram showing proportional mean major-ion composition, by study, for groundwater samples collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2008–12...... 26 7. Map showing distribution ranges of median concentrations of selected constituents measured in groundwater samples from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 27 v

8. Bivariate graphs showing the relations between concentrations of dissolved oxygen and as compared to selected properties value or constituents measured in groundwater-quality samples collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 30

Tables

1. Laboratory analyses for groundwater samples collected from wells and for surface-water sample collected from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 7 2. Physical properties, inorganic constituents, and other constituents analyzed in groundwater and surface-water samples in the field or at the U.S. Geological Survey National Water Quality Laboratory for samples collected at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 9 3. Volatile organic compounds, gasoline-range organics, and diesel-range organics analyzed in groundwater and surface-water samples at TestAmerica Laboratories, Inc., laboratory reporting levels, and related U.S. Environmental Protection Agency drinking-water standards and health advisories...... 12 4. Replicate data for major ions, nutrients, dissolved organic carbon, trace elements, and triazoles in groundwater samples from wells at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 15 5. Horizontal hydraulic gradients calculated for selected water-level measurement events at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 22 6. Results of groundwater-velocity calculations using hydraulic conductivity values of the Snake River alluvial aquifer at Teton Village and the Aspens...... 22 7. Summary of physical properties and inorganic groundwater-quality data collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 24 8. Assignment of redox categories and processes for groundwater samples from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 29 Appendix 1. Well construction and related ancillary information for wells used for data collection at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 38 Appendix 2. Water-level data and related ancillary information for measurements collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 39 Appendix 3. Inorganic and organic constituents in blank samples collected for followup study at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 42 Appendix 4. Physical properties measured in groundwater samples from wells and a surface-water sample from irrigation ditch at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 45 Appendix 5. Analytical results for chemical oxygen demand, major ions, trace elements, nutrients, dissolved organic carbon, and stable isotopes in groundwater samples from wells and a surface-water sample from irrigation ditch at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 46 Appendix 6. Analyses for dissolved gases in groundwater samples from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 48 vi

Appendix 7. Analytical results for volatile organic compounds, gasoline-range organics, and diesel-range organics in groundwater samples from wells and a surface-water sample from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 49 Appendix 8. Analytical results for triazoles in groundwater samples from wells and a surface-water sample from irrigation ditch at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012...... 55

Conversion Factors

Inch/Pound to SI Multiply By To obtain Length inch (in.) 2.54 centimeter (cm) inch (in.) 25.4 millimeter (mm) foot (ft) 0.3048 meter (m) mile (mi) 1.609 kilometer (km) Area acre 4,047 square meter (m2)

Temperature can be converted to degrees Fahrenheit (°F) or degrees Celsius (°C) as follows: °F = 9/5 (°C) + 32 °C = 5/9 (°F – 32) Vertical coordinate information is referenced to the North American Vertical Datum of 1988 (NAVD 88), with the exception of figure 5, which is referenced to the National Geodetic Vertical Datum of 1929 (NGVD 29). Horizontal coordinate information is referenced to the North American Datum of 1983 (NAD 83). Altitude, as used in this report, refers to distance above the vertical datum. Specific conductance is given in microsiemens per centimeter at 25 degrees Celsius (µS/cm at 25 °C). Concentrations of chemical constituents in water are given either in milligrams per liter (mg/L) or micrograms per liter (µg/L). Water year is the 12-month period, October 1 through September 30, and is designated by the calendar year in which it ends. vii

Abbreviations and Acronyms < less than ± plus or minus 4-MeBT 4-methyl-1H-benzotriazole 5-MeBT 5-methyl-1H-benzotriazole ADAF aircraft deicing/anti-icing fluid

CaCO3 calcium carbonate

CH4 methane COD chemical oxygen demand DOC dissolved organic carbon DRO diesel-range organic E estimated value e-tape electronic tape Fe2+ ferrous iron GRO gasoline-range organic

H2S dihydrogen sulfide (aqueous) HS– hydrogen sulfide IRL interim reporting level JHA Jackson Hole Airport LOD limit of detection (Wisconsin State Laboratory of Hygiene) LRL laboratory reporting level MCL Maximum Contaminant Level (U.S. Environmental Protection Agency) MDL method detection limit Mn2+ manganese MRL minimum reporting level

– NO3 nitrate NWIS National Water Information System (U.S. Geological Survey) NWQL National Water Quality Laboratory (U.S. Geological Survey)

O2 oxygen PVC polyvinyl chloride redox reduction and oxidation RPD relative percent difference S2– sulfide SMCL Secondary Maximum Contaminant Level (U.S. Environmental Protection Agency)

2– SO4 sulfate USEPA U.S. Environmental Protection Agency USGS U.S. Geological Survey VOC volatile organic compound WSLH Wisconsin State Laboratory of Hygiene

Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming, Water Years 2011 and 2012

By Peter R. Wright

Abstract samples. The quality of groundwater in the alluvial aquifer generally was suitable for domestic and other uses; however, The hydrogeology and water quality of the Snake River dissolved iron and manganese were detected in samples alluvial aquifer at the Jackson Hole Airport in northwest Wyo- from many of the monitor wells at concentrations exceeding U.S. Environmental Protection Agency secondary maximum ming was studied by the U.S. Geological Survey, in coopera- contaminant levels. Iron and manganese likely are both natural tion with the Jackson Hole Airport Board, during water years components of the geologic materials in the area and may have 2011 and 2012 as part of a followup to a previous baseline become mobilized in the aquifer because of redox processes. study during September 2008 through June 2009. Hydro- Additionally, measurements of dissolved-oxygen concentra- geologic conditions were characterized using data collected tions and analyses of major ions and nutrients indicate reduc- from 19 Jackson Hole Airport wells. Groundwater levels are ing conditions exist at 7 of the 10 wells sampled. summarized in this report and the direction of groundwater Measurements of dissolved-oxygen concentrations (less flow, hydraulic gradients, and estimated groundwater velocity than 0.1 to 9 milligrams per liter) indicated some variability in rates in the Snake River alluvial aquifer underlying the study the oxygen content of the aquifer. Dissolved-oxygen con- area are presented. Analytical results of groundwater samples centrations in samples from 3 of the 10 wells indicated oxic collected from 10 wells during water years 2011 and 2012 are conditions in the aquifer, whereas low dissolved-oxygen con- presented and summarized. centrations (less than 1 milligram per liter) in samples from The water table at Jackson Hole Airport was lowest in 7 wells indicated anoxic conditions. Nutrients were present in early spring and reached its peak in July or August, with an low concentrations in all samples collected. Nitrate plus nitrite increase of 12.5 to 15.5 feet between April and July 2011. was detected in samples from 6 of the 10 monitored wells, Groundwater flow was predominantly horizontal but generally whereas dissolved ammonia was detected in small concentra- had the hydraulic potential for downward flow. Groundwater tions in 8 of the 10 monitored wells. Dissolved organic carbon flow within the Snake River alluvial aquifer at the airport concentrations generally were low. At least one dissolved was from the northeast to the west-southwest, with horizontal organic carbon concentration was quantified by the laboratory velocities estimated to be about 25 to 68 feet per day. This in samples from all 10 wells; one of the concentrations was range of velocities slightly is broader than the range deter- an order of magnitude higher than other detected dissolved mined in the previous study and likely is due to variability in organic carbon concentrations, and slightly exceeded the esti- the local climate. The travel time from the farthest upgradient mated range for natural groundwater. well to the farthest downgradient well was approximately 52 Samples were collected for analyses of dissolved gases, to 142 days. This estimate only describes the average move- and field analyses of ferrous iron, hydrogen sulfide, and low- ment of groundwater, and some solutes may move at a differ- level dissolved oxygen were completed to better understand ent rate than groundwater through the aquifer. the redox conditions of the alluvial aquifer. Dissolved gas The quality of the water in the alluvial aquifer generally analyses confirmed low concentrations of dissolved oxygen was considered good. Water from the alluvial aquifer was in samples from wells where reducing conditions exist and fresh, hard to very hard, and dominated by calcium carbonate. indicated the presence of methane gas in samples from several No constituents were detected at concentrations exceeding wells. Redox processes in the alluvial aquifer were identified U.S. Environmental Protection Agency maximum contaminant using a model designed to use a multiple-lines-of-evidence levels or health advisories; however, reduction and oxidation approach to distinguish reduction processes. Results of redox (redox) measurements indicate oxygen-poor water in many analyses indicate iron reduction was the dominant redox pro- of the wells. Gasoline-range organics, three volatile organic cess; however, the model indicated manganese reduction and compounds, and triazoles were detected in some groundwater methanogenesis also were taking place in the aquifer. 2 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Each set of samples collected during this study included and high rates of hydraulic conductivity (Hamerlinck and analysis of at least two, but often many anthropogenic Arneson, 1998). compounds. During the previous 2008–09 study at Jackson Of particular interest is whether or not deicing and anti- Hole Airport, diesel-range organics were measured in small icing compounds used at the airport are being transported into (estimated) concentrations in several samples. Samples col- the alluvial aquifer. Studies of water quality near other airports lected from all 10 wells sampled during the 2011–12 study in the United States and Norway have documented compo- were analyzed for diesel-range organics, and there were no nents of aircraft deicing/anti-icing fluid (ADAF) in airport detections; however, several other anthropogenic compounds snowbanks (Corsi and others, 2006a), surface-water runoff were detected in groundwater samples during water years (Corsi and others, 2001), and shallow groundwater (Breedveld 2011—12 that were not detected during the previous 2008–09 and others, 2002, 2003; Cancilla and others, 1998, 2003a). study. Gasoline-range organics, benzene, ethylbenzene, and Decreased dissolved-oxygen conditions were determined to be total xylene were each detected (but reported as estimated associated with ADAFs (Cancilla and others, 1998; Corsi and concentrations) in at least one groundwater sample. These others, 2001; Corsi and others, 2006a, 2006b). These stud- compounds were not detected during the previous study or ies have determined that glycols, the primary ingredient in consistently during this study. Several possible reasons these ADAFs, have high biochemical oxygen demand, creating the compounds were not detected consistently include (1) these potential for oxygen depletion in receiving waters (Corsi and compounds are present in the aquifer at concentrations near others, 2001). In addition to glycols, ADAFs contain vari- the analytical method detection limit and are difficult to detect, ous performance-enhancement additives, which also can be (2) these compounds were not from a persistent source during isolated in environmental waters. During 2008 and 2009, the this study, and (3) these compounds were detected because USGS completed a baseline study to characterize the hydro- of contamination introduced during sampling or analysis. geology and groundwater quality of the Snake River alluvial During water years 2011–2012, groundwater samples were aquifer in upgradient and downgradient parts of the aquifer analyzed for triazoles, specifically benzotriazole, 4-methyl- underlying the JHA (Wright, 2010). In that study, Wright 1H-benzotriazole, and 5-methyl-1H-benzotriazole. Triazoles (2010) reported the detection of chemical conditions indica- are anthropogenic compounds often used as an additive in tive of the presence of organic compounds, such as ADAFs or deicing and anti-icing fluids as a corrosion inhibitor, and can their breakdown products, in groundwater downgradient from be detected at lower laboratory reporting levels than glycols, historical deicing application areas. A zone of highly reduced which previously had not been detected. Two of the three groundwater was observed downgradient from the deicing triazoles measured, 4-methyl-1H-benzotriazole and 5-methyl- areas, but the reason why dissolved oxygen was depleted and 1H-benzotriazole, were detected at low concentrations in methane was detected could not be determined. groundwater at 7 of the 10 wells sampled. The detection of To achieve a better understanding of such groundwater- triazole compounds in groundwater downgradient from airport quality issues and changes in flow conditions at the JHA, the operations makes it unlikely there is a natural cause for the USGS, in cooperation with the Jackson Hole Airport Board, high rates of reduction present in many airport monitor wells. conducted a followup study of groundwater conditions at It is more likely that aircraft deicers, anti-icers, or pavement the airport during water years 2011–12; a water year is the deicers have seeped into the groundwater system and caused 12-month period from October 1 through September 30, and is the reducing conditions. designated by the calendar year in which it ends. The objective of this followup study was to further characterize the hydrogeology and groundwater quality of the Snake River aquifer in Introduction upgradient and downgradient parts of the aquifer underlying the airport and facilities. The Snake River alluvial aquifer is located in the Snake River valley in northwestern Wyoming, including Grand Purpose and Scope Teton National Park, in an area known as Jackson Hole. This alluvial aquifer is used for domestic, public supply, com- The purpose of this report is to describe the hydrogeol- mercial, livestock, and irrigation purposes (Nolan and Miller, ogy and water quality within the alluvial aquifer underlying 1995). In 2005, the U.S. Geological Survey (USGS) estimated the JHA during water years 2011 and 2012. Water-quality that 98 percent of the water used for domestic and public samples were collected during four time periods (June, July, supply in Teton County was groundwater (U.S. Geological and November 2011 and April 2012), each representing differ- Survey, 2005). Water from this aquifer is used for domestic ent hydrogeologic conditions and different airport-use periods. and commercial purposes by the Jackson Hole Airport (JHA) Hydrogeologic characteristics, including the direction of and nearby residents. Airport activities and facilities have groundwater flow, hydraulic gradients, estimated groundwater- the potential to affect water quality in the aquifer. The JHA flow rates, and water-quality conditions for major-ion chem- is located in an area of high vulnerability to groundwater istry, nutrients, trace elements, volatile organic compounds contamination which is due to a high water table, coarse soils, (VOCs), gasoline-range organics (GROs), diesel-range Study Design 3 organics (DROs), and triazoles, upgradient and downgradient (°F) in January to 80.6 °F in July with an annual average of from airport activities and facilities, are described. Reduction 36.9 °F from 1958–2012 (Western Regional Climate Center, and oxidation processes (redox) are characterized. Conclu- 2012). Mean monthly precipitation data, also collected at the sions drawn from study results are described. Much of the climate station in Moose, Wyo., ranged from 1.15 inches (in.) hydrogeologic and water-quality data presented in Wright in July to 2.62 in. during January with an annual average of (2010) will be referenced in this report. 21.33 in. for the period 1958–2012 (Western Regional Climate Center, 2012). Much of the precipitation in the Jackson Hole area is snowfall. On average, snow falls 10 months of the year Description of Study Area with an average snowfall of 172.2 in. at Moose, Wyo. (West- The JHA is located in the southern part of Jackson Hole, ern Regional Climate Center, 2012). Leading up to the study a semiarid, high-altitude valley in northwestern Wyoming (2010 and early 2011), precipitation generally was well above (fig. 1). Located approximately 8 miles (mi) north of the average, whereas precipitation was near average during June town of Jackson, JHA is the busiest commercial airport in 2011–April 2012. Wyoming; in 2008, 3,904 flights carried more than 600,000 passengers (Michelle Buschow, Jackson Hole Airport, written commun., 2009). The airport is unique in that it is located Study Design within Grand Teton National Park, along the park’s south- western boundary. The airport is at an altitude of about 6,400 Water-quality sampling and water-level monitoring feet (ft) above the North American Vertical Datum of 1988 were conducted at 10 monitor wells: 5 existing monitor wells (NAVD 88), covers an area of 533 acres, and has one runway installed for the baseline study (Wright, 2010), and 5 new and one taxiway (Jackson Hole Airport, 2009). monitor wells installed to help expand knowledge of local The JHA is located east of the Snake River on Snake hydrogeologic and water-quality characteristics (fig. 2). In River terrace deposits (Pierce and Good, 1992). These terrace addition to the 10 monitor wells, 9 existing production wells deposits consist of Quaternary-age unconsolidated gravel, were selected for water-level monitoring. The hydrogeology pediment, and fan deposits that are saturated and collectively of the Snake River alluvial aquifer underlying the JHA was constitute a large water-table aquifer throughout the eastern characterized using water levels collected from these 19 wells part of Grand Teton National Park and the Jackson Hole area during water years 2011 and 2012. The water quality of the (Nolan and Miller, 1995; Nolan and others, 1998). The aquifer Snake River alluvial aquifer was determined from water- informally is named the “Jackson aquifer” (Nolan and Miller, quality samples collected at the 10 monitoring wells (fig. 2, 1995) and is referred to as the “Snake River alluvial aquifer” appendix 1). in this report. The thickness of the Snake River alluvial aquifer Eight of the 10 monitor wells sampled during this study in the vicinity of the airport is estimated to be 200 to 250 ft are screened near the water table, and two monitoring wells (Nolan and others, 1998) and is the primary water supply for (JH–1.5D and JH–3D) are completed in the deeper part of JHA and area residents. the aquifer (appendix 1). As part of the baseline study, five The Snake River alluvial aquifer is unconfined, and depth wells had been installed along the direction of groundwater to water ranged from less than 1 ft to 233.91 ft below land flow based on published potentiometric-surface contour maps surface with a median depth to water of 10.78 ft below land (Kumar and Associates, written commun., 1993; Nolan and surface (Nolan and Miller, 1995). Depth to water varies with Miller, 1995; Wright, 2010). To summarize these existing topography and is shallowest near bodies of surface water. wells, well JH–1 is north and east of current (2013) airport Recharge of the alluvial aquifer generally is by infiltration operations (upgradient), just east of the Teton Interagency of precipitation, streamflow leakage, and irrigation water, Helitack Crew operations center (fig. 2). Three wells (JH–2, and migration of deep groundwater near fault zones (Nolan JH–3, and JH–4) are along the south and west airport bound- and Miller, 1995). Groundwater in the Snake River alluvial ary and represent downgradient conditions of current and aquifer generally follows the topography, moving from high planned airport operations, and a deep well (JH–3D) is adja- altitudes toward the Snake River and to the southwest through cent to well JH–3 along the south and west airport boundary the Snake River valley (Nolan and Miller, 1995). The direc- (fig. 2). tion of groundwater flow in the Snake River alluvial aquifer Initially, four additional wells were installed for this fol- at the JHA is from the northeast to the southwest (Kumar and lowup study. Two wells were installed lateral [JH–2.5 (south) Associates, written commun., 1993; Nolan and Miller, 1995; and JH–3.5 (north)] to wells JH–3 and JH–3D (well cluster 3), Wright, 2010). and a water table/deep well pair [wells JH–1.5 and JH–1.5D The study area is in the Middle Rockies ecoregion, which (wells cluster 1.5)] was installed upgradient from well clus- is a temperate, semiarid steppe regime (Chapman and others, ter 3 (fig. 2). During this followup study, it was determined the 2004). Climate conditions in the Jackson Hole area vary with new shallow wells did not extend deep enough into the aquifer changes in season and altitude. Mean monthly temperatures to contain water throughout the year. During October 2011 one at the climate station in Moose, Wyoming, located approxi- new, deeper, water-table well (JH–1.5R) was installed near mately 4 mi north of JHA, ranged from 0.9 degree Fahrenheit wells JH–1.5 and JH–1.5D. 4 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

111°00’ 110°45’ 110°30’

287 Emma Matilda Lake Ja ck so n La Moran ke 287 TARGHEE Leigh Lake NATIONAL E FOREST G N GRAND TETON

A NATIONAL PARK Spread

Jenny Lake Creek Teton Creek JACKSON

43°45’ HOLE N

O y T e l l E a V 26 T r e 89 v Creek i R 191 e k a n Ditch S BRIDGER-TETON Phelps Moose Lower Slide NATIONAL Lake Jackson Hole Airport Lake IDAHO River FOREST WYOMING Granite Creek Ventre

Teton Gros Village National

10,927 Moose Creek GROS VENTRE RANGE Rendezvous Elk River Peak Creek Flat Creek Aspens Refuge

22 Wilson Snake SN 43°30’ A KE R IV ER Jackson R Mosquito Fish AN GE Cache Creek 191 HOBACK RANGE Creek

Base from U.S. Census Bureau, 2001 EXPLANATION Lambert Conformal Conic projection Approximate boundary of Yellowstone National Park Standard parallels 43°N and 44°N A B

Jackson Hole valley S Central meridian 110°30′W A R North American Datum of 1983 (NAD 83) Boundary of Grand Teton Map area O K A National Park Washakie Range RA NG 0 5 10 MILES E Jackson Grand Hole Teton WYOMING 0 5 10 KILOMETERS Airport National Park

Figure 1. Location of Jackson Hole Airport in the Jackson Hole valley, Wyoming. Study Design 5

Control tower

Spring Gulch Road

Teton Interagency Helitack Crew operations center JH–1

JH–4

Terminal

Airport parking

E. Trap Club Rd.

North hangar Hangar 1

Fuel farm JH–3.5 Hangar 2 Airport entrance JH–1.5 JH–1.5R Middle E ast JH–1.5D hangar Air JH–3 port Road Hangar 3 Leach field JH–3D South Side Septic tanks fuel farm Rental car buildings JH–2.5 Leach field Ponderosa Dr. Septic tank South hangar

Spring Gulch Road Auto garage

Jackson Hole aviation Hangar 5 rotate hangar

Hangar

Irrigation ditch

Ponderosa Dr. JH–2 EXPLANATION Fence Hangar 5 Production well where groundwater level was measured and identifier

JH–2 Well installed for baseline study where groundwater level was measured and water-quality samples were collected and identifier 0 500 1,000 FEET JH–2.5 Well installed for followup study where groundwater 0 150 300 METERS level was measured and water-quality samples were collected and identifier Figure 2. Location of wells used in the study area for data Irrigation ditch surface-water sampling site collection, Jackson Hole Airport, Jackson, Wyoming. 6 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Groundwater samples were collected four times from Methods of Data Collection and each of the monitor wells with two exceptions. First, wells JH–1.5 and JH–1.5R were each only sampled twice. Since Analysis well JH–1.5R was installed very close to well JH–1.5, was screened across the same aquifer (extending several feet Methods used for monitor well construction, water-level deeper) and was a direct replacement for well JH–1.5, the measurement, analysis of hydrogeologic data, and collection hydrogeologic and water-quality data collected from these and analysis of groundwater, surface-water, and quality- two wells have been combined, and treated as one well for control samples are described herein. Technical guide- data analysis in this report. Second, during the April 2012 lines applicable to this study are documented in the USGS sampling event, not enough water was in well JH–3.5 to col- “National Field Manual for the Collection of Water-Quality lect a sample because of a low water table. One surface-water Data” (U.S. Geological Survey, variously dated) and “Ground- quality sample was collected in June 2011 from the irriga- water Technical Procedures of the U.S. Geological Survey” tion ditch that flows across the southern end of the airport (Cunningham and Schalk, 2011). To record data in the USGS (fig. 2).Water-quality results described in this report are for National Water Information System (NWIS), each site must samples collected between June 2011 and April 2012; how- be established with at least a minimum set of data (Cunning- ever, where appropriate, data collected during the baseline ham and Schalk, 2011). This minimum dataset includes well study (2008–09) described in Wright (2010) are used for construction information, documentation of well location, comparison. established measuring point and land surface datums, and field Laboratory analyses varied by well and sampling date measurements of well depth and water level. The techniques and are listed in table 1. Groundwater samples were collected used to accomplish the site inventories are included through- from existing and new wells to further describe basic ground- out the “Methods of Data Collection and Analysis” section of water geochemistry, including major inorganics [major ions, the report. dissolved solids, silica, and the trace elements manganese and iron], nutrients (nitrite, nitrate, ammonia, total nitrogen, total Well Construction and Ancillary Information phosphorus, and orthophosphate), chemical oxygen demand (COD), and dissolved organic carbon (DOC). Water-quality Many wells have been installed to monitor the hydro- results for the baseline study (Wright, 2010) did not indicate geology and quality of groundwater underlying the JHA. the presence of VOCs or GRO compounds at wells JH–1, Monitoring wells installed for this study were drilled using a JH–2, JH–3, JH–3D, or JH–4; therefore, samples from these dual rotary drill rig. Well construction and related ancillary wells were not reanalyzed for these constituents. However, information for wells used during this study are presented in samples from newly drilled wells (JH–1.5, JH–1.5R, JH–1.5D, appendix 1. Four new monitor wells were installed during the JH–2.5, and JH–3.5) were analyzed for these constituents to summer of 2010 as part of this followup study. Well JH–1.5D define baseline conditions in these new areas and for com- was modified after initial installation with no screen to include parison to results for these same constituents as presented in a 10-ft screened interval, and a fifth well, JH–1.5R, was Wright (2010) (table 1). DROs were reanalyzed as part of the installed in October 2011 nearby at a depth approximately followup study to confirm or refute the presence of DROs as 10 ft deeper than well JH–1.5 to ensure there would be water previously reported (Wright, 2010). in the shallow (water table) well at this location throughout the Because glycol compounds were not detected during the year. Water-table wells were constructed with 2-in. diameter, baseline study (Wright, 2010), samples were not analyzed for flush-jointed polyvinyl chloride (PVC) casing and well screen. glycols. Instead, samples were analyzed for triazoles, specifi- Well screens used to construct the wells were 10 or 20 ft long cally benzotriazole, 4-methyl-1H-benzotriazole (4-MeBT) and (appendix 1) and set at depths about 10 to 15 ft below and 5-methyl-1H-benzotriazole (5-MeBT). Triazoles are a class 5 ft above the water-table surface. This allowed the wells of chemicals historically used in ADAFs as corrosion inhibi- to “straddle” the water table, allowing for measurement of tors and have been shown to increase the toxicity of ADAF to some seasonal changes in the water-table altitude and allow- aquatic organisms (Pillard, 1995; Cancilla and others, 1997; ing for determination of the presence of possible groundwater and Cornell and others, 2000). These compounds can be contaminants, such as petroleum fuels that can float on or near detected at laboratory reporting levels two orders of magni- the water-table surface. A deep well (JH–1.5D) was drilled tude lower than glycols, and were used in this investigation to to about 95 ft of depth and installed adjacent to well JH–1.5. determine if deicing compounds are a source of organic carbon Well JH–1.5D initially was installed in the same manner as associated with the zone of reduced groundwater described in well JH–3D; well JH–3D is not perforated or screened and Wright (2010). Additional water-quality data (ferrous iron, dis- therefore acts as a piezometer; however, as described above, solved oxygen, and sulfide analyzed in the field during sample this well was modified to include a PVC well screen. The collection) were collected from wells with low [less than driller installed a 2-in. diameter, flush-jointed PVC casing with (<) 1 milligram per liter (mg/L)] dissolved-oxygen concentra- 10 ft of well screen and removed the 6-in. steel casing. Before tions to better understand the redox processes at these wells. sampling, all of the new and updated monitoring wells were

Methods of Data Collection and Analysis 7 Apr. 2012 Apr.

------Nov. 2011 Nov.

------July 2011 July

------June 2011 June

Irrigation ditch -- -- X X X X X X X X Apr. 2012 Apr.

------X X X X X X Nov. 2011 Nov.

------X X July 2011 July

JH–4 ------X X X June 2011 June

------X X X X Apr. 2012 Apr.

-- -- N N N N N N N N Nov. 2011 Nov.

------X X July 2011 July

-- -- X X X X X X X X JH–3.5

ganic carbon; VOC, volatile organic compound; VOC, volatile organic ganic carbon; June 2011 June

-- X X X X X X X X X Apr. 2012 Apr.

------X X X X X X Nov. 2011 Nov.

------X X July 2011 July

------X X X X X X JH–3D June 2011 June

------X X X X X X X Apr. 2012 Apr.

------X X X X X X Nov. 2011 Nov.

------X X July 2011 July

JH–3 ------X X X X X X June 2011 June

------X X X X X X X Apr. 2012 Apr.

-- -- X X X X X X X X Nov. 2011 Nov.

------X X July 2011 July

-- -- X X X X X X X X JH–2.5 June 2011 June

-- X X X X X X X X X Apr. 2012 Apr.

TestAmerica Laboratories TestAmerica ------X X X X X X Wells sampled at the Jackson Hole Airport Wells Nov. 2011 Nov. ------X X

Wisconsin State Laboratory of Hygiene USGS National Water Quality Laboratory USGS National Water July 2011 July

JH–2 USGS Reston Chlorofluorocarbon Laboratory ------X X X X June 2011 June

------X X X X X Apr. 2012 Apr.

-- -- X X X X X X X X Nov. 2011 Nov.

------X X X X X July 2011 July

-- -- X X X X X X X X

JH–1.5D June 2011 June

-- X X X X X X X X X Apr. 2012 Apr.

-- -- X X X X X X X X Nov. 2011 Nov.

------X X JH–1.5R July 2011 July

-- -- X X X X X X X X June 2011 June

-- X X X X X X X X X JH–1.5 Apr. 2012 Apr.

------X X X X X X Nov. 2011 Nov.

------X X July 2011 July

JH–1 ------X X X June 2011 June ------X X X X Laboratory analyses for groundwater samples collected from wells and surface-water sample irrigation ditch at the Jackson Hole Airport, Jackson,

manganese gases Constituent COD Major ions Nutrients DOC Iron and VOCs GROs DROs Triazoles Dissolved Table 1. Table water years 2011 and 2012. Wyoming, [USGS, U.S. Geological Survey; --, not analyzed; X, N, sample was planned but collected; COD, chemical oxygen demand; DOC, dissolved or DRO, diesel range organic] GRO, gasoline range organic; 8 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming pumped or “developed” using methods described in Lapham water-level data from three wells to perform a three-point and others (1995) to remove artifacts associated with drilling, calculation (Heath, 1983), located in a triangular arrangement. such as drilling fluids, to provide water representative of the Data necessary for these calculations included water-level aquifer being sampled, and to improve movement of water to altitude (appendix 2) and the linear distance between wells the well. (approximated from a USGS 7.5-minute, 1:24,000-scale Well locations and altitudes were determined by the topographic map). An average groundwater velocity can be USGS or a survey contractor for each of the monitoring wells. estimated if the horizontal hydraulic conductivity, effective Well locations were determined by the USGS using a global porosity, and hydraulic gradient are known, with the assump- positioning system that reported latitude and longitude using tion that groundwater flow is perpendicular to the water-table the North American Datum of 1983 (NAD 83) with hori- contours and the aquifer is homogeneous and isotropic. A zontal accuracy of less than plus or minus (±) 49 ft (15 m) groundwater velocity was estimated using a hydraulic conduc- (Garmin, 2004). Altitudes for all of the monitoring wells tivity of 2,900 and 1,200 feet per day (Nelson Engineering, installed for this study were determined using conventional 1992), a porosity of 30 percent, and the average hydraulic surveying methods. gradient calculated for each water-level measurement event using the methods described in Heath (1983) and presented in Water-Level Measurement Wright (2010). Discrete water levels were measured during each site Groundwater and Surface-Water Sampling and visit to the airport (appendix 2), and hourly water levels were collected at selected wells during and after other field activi- Analysis ties were completed. Discrete water levels were measured Groundwater samples were collected during four time with a calibrated electric tape (e-tape) when the well casing periods, each event representing different hydrogeologic con- was clear or with a calibrated steel tape when well pump and ditions and airport-use periods. Sampling methods are briefly power cables were present. A detailed description of the meth- described herein. Samples were analyzed for many different ods used to measure water levels by use of e-tape or steel tape constituents—some of these constituents were analyzed in the are documented in Cunningham and Schalk (2011). Replicate field, whereas other constituents were analyzed in a laboratory. measurements were made during each visit to ensure the water Analytical laboratories, a brief description of the constituents level measured was the correct water level. Water levels were each laboratory analyzed, and a description of laboratory measured to one-hundredth of a foot. reporting levels, are included in this section of the report. During February 2009, continuous water-level record- Groundwater samples were collected and processed in a ers were installed in monitoring wells JH–1, JH–2, JH–3, and mobile water-quality laboratory in accordance with standard JH–4. These instruments were installed by and continue to be USGS methods described in the USGS field manual (U.S. maintained by the Teton Conservation District. These self- Geological Survey, variously dated). Water was pumped from contained pressure transducer/temperature/data logging units each well through a sampling manifold and a flow-through are vented, allowing for changes in barometric pressure, and chamber in the mobile laboratory until at least three well- are accurate to ±0.012 ft (In-Situ, Inc., 2007, p. 23). Discrete casing volumes had been removed and measurements of phys- water-level measurements were collected each time data were ical properties of dissolved oxygen, pH, specific conductance, downloaded and during each site visit (appendix 2) to verify and temperature stabilized. These physical properties (table 2) proper reading of the instrument. The Teton Conservation District provided continuous and discrete water-level measure- were measured in the field as part of sample collection using ments to the USGS for use in this study. Continuous water- methods described in the USGS field manual (U.S. Geologi- level data collected through water year 2012 were checked cal Survey, variously dated). Alkalinity was determined using by USGS personnel, entered into the USGS NWIS database, incremental titration of a filtered water sample with sulfuric and when logged instrument readings did not match discrete acid as described in the USGS field manual (U.S. Geologi- water-level measurements, a datum correction was applied to cal Survey, variously dated). Samples collected for analyses the applicable period of record. of major ions, selected nutrients, selected trace elements, and dissolved organic carbon were filtered by passing sample water through a pre-conditioned 0.45-micrometer, nominal- Water-Table Contours, Hydraulic Gradient, and pore-size, disposable capsule filter. In this report, constituents Groundwater Velocity in filtered water samples are referred to as dissolved. Constitu- ents in unfiltered water samples are referred to as total. Water-table contours were constructed, and direction of One surface-water quality sample was collected from groundwater flow, hydraulic gradient and groundwater veloc- the irrigation ditch that flows across the southern end of ity were calculated using methods described in Heath (1983) the airport (fig. 2) and analyzed for selected constituents as and presented in Wright (2010). Each set of calculations for listed in table 1. This surface-water sample was collected direction of groundwater flow and hydraulic gradient required and processed in accordance with standard USGS methods Methods of Data Collection and Analysis 9

Table 2. Physical properties, inorganic constituents, and other constituents analyzed in groundwater and surface-water samples in the field or at the U.S. Geological Survey National Water Quality Laboratory for samples collected at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

[--, not applicable; MRL, minimum reporting level; LTMDL, long-term method detection level; MDL, method detection level; IRL, interim reporting level; LRL, laboratory reporting level]

Sampling 2011–12 Physical property or Unit of measure inorganic constituent Reporting level Reporting level (unit of measure) type Physical properties (field analyses) Dissolved oxygen milligrams per liter -- -- pH standard units -- -- Specific conductance microsiemens per centimeter at 25 degrees Celsius -- -- Water temperature degrees Celsius -- -- Turbidity1 nephelometric turbidity ratio units -- -- Major ions and related water-quality characteristics Dissolved solids, residue on evaporation milligrams per liter 20 MRL at 180 degrees Celsius Calcium, dissolved milligrams per liter 0.044 LTMDL Magnesium, dissolved milligrams per liter 0.022 LTMDL Potassium, dissolved milligrams per liter 0.06 LTMDL Sodium, dissolved milligrams per liter 0.12 LTMDL Alkalinity, dissolved milligrams per liter, as calcium carbonate -- -- Bicarbonate, dissolved milligrams per liter -- -- Hardness, total milligrams per liter, as calcium carbonate -- -- Bromide, dissolved milligrams per liter 0.02 MDL Chloride, dissolved milligrams per liter 0.12 LTMDL Fluoride, dissolved milligrams per liter 0.08 LTMDL Silica, dissolved milligrams per liter 0.036 LTMDL Sulfate, dissolved milligrams per liter 0.18 LTMDL Nutrients Ammonia, dissolved milligrams per liter as nitrogen 0.02 LTMDL Nitrate plus nitrite, dissolved milligrams per liter as nitrogen 0.08 MDL Nitrite, dissolved milligrams per liter as nitrogen 0.002 IRL Orthophosphate, dissolved milligrams per liter as phosphorus 0.008 LRL Phosphorus, total milligrams per liter 0.008 LRL Nitrogen, total milligrams per liter 0.1 LRL Trace elements1 Iron, dissolved micrograms per liter 8.0 LTMDL Manganese, dissolved micrograms per liter 0.32 LTMDL Other analyses Chemical oxygen demand milligrams per liter 10 MRL Organic carbon, dissolved milligrams per liter 0.46 LTMDL 1Analyzed in groundwater samples only. 10 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming described in the USGS field manual (U.S. Geological Sur- low-range dissolved oxygen; HACH® method 8146, which is vey, variously dated). To minimize sample disturbance, VOC the 1,10-phenanthroline method using AccuVac ampoules for sample containers were filled directly from the irrigation ditch. ferrous iron; and HACH® method 8131, which is a methylene Remaining sample containers were filled from a churn splitter blue method for sulfide (HACH, 2007). containing a representative surface-water sample collected Each of the laboratories described previously reported from the irrigation ditch using a DH-81 isokinetic sampler and analytical results in accordance with their protocols. This para- the equal-width-increment sampling technique (U.S. Geologi- graph generally describes how data included in this report are cal Survey, variously dated). Processing of the surface-water reported. The less than symbol (<) indicates that the chemical sample was similar to groundwater samples. The ditch sample was not detected. For data reported by the NWQL, the USGS was analyzed for all the same constituents as groundwater Reston Chlorofluorocarbon Laboratory, and TestAmerica samples, except for dissolved gases. Laboratories, the value following the less than (<) symbol is The USGS National Water Quality Laboratory (NWQL) the laboratory reporting level (LRL), interim reporting level in Denver, Colorado, analyzed water samples for major ions, (IRL), or the minimum reporting level (MRL) associated with COD, DOC, nutrients, and trace elements of iron and manga- that analysis. The LRL can have various definitions, depend- nese. Major ions and trace elements (table 2) were analyzed ing on the laboratory, but for water-quality data reported by using ion-exchange chromatography or inductively coupled the NWQL, the LRL generally is equal to twice the yearly plasma-atomic-emission spectroscopy (Fishman and Fried- determined long-term method detection level (Childress and man, 1989; Fishman, 1993). Nutrients and COD were ana- others, 1999). The IRL, such as for dissolved nitrite (table 2), lyzed using colorimetry (Fishman, 1993). DOC was analyzed is a temporary reporting level used for new or custom sched- using ultraviolet light-promoted persulfate oxidation and ules when long-term method detection level data are unavail- infrared spectrometry (Brenton and Arnett, 1993). able and a LRL has not yet been established (U.S. Geological TestAmerica Laboratories, Inc., in Denver, Colo., was Survey, 2004). The MRL, as defined by the NWQL, is the contracted to analyze water samples for VOCs, GRO, and smallest measured concentration of a substance that can be DRO (table 3) using U.S. Environmental Protection Agency measured reliably by using a given analytical method (Timme, (USEPA) methods. VOCs were analyzed using USEPA 1995). For triazole data reported by the WSLH, the value method 524.2 (Munch, 1995), GROs were analyzed using following the less than (<) symbol is the limit of detection USEPA SW846 method 8021/8015B (U.S. Environmental (LOD) or detection limit, defined as the lowest concentration Protection Agency, 1996a, 1996b), and DROs were analyzed level that can be determined to be statistically different from a using USEPA SW846 method 8015B (U.S. Environmental blank sample with 99-percent confidence (Wisconsin Depart-

Protection Agency, 1996a) in the C10–C36 ranges (table 3). ment of Natural Resources, 1996). The LOD approximately is The Wisconsin State Laboratory of Hygiene (WSLH) equal to the method detection limit (MDL) for those analyses was contracted to analyze water samples for benzotriazole, for which the MDL can be calculated. Some water-quality 4-MeBT and 5-MeBT, generally referred to as triazoles in this results, especially those for organic compounds in this study, report. Groundwater samples collected from each well for are qualified with an “E” or are reported as a less than (<) all sampling events during water years 2011 and 2012 were value. The “E” remark code indicates the value is estimated analyzed for triazoles. The one surface-water sample collected and less than the LRL, but equal to or greater than the labora- from the irrigation ditch in June 2011 also was analyzed for tory method detection limit. Values commonly are estimated triazoles. The WSLH has developed a high performance/liquid when the value is greater than the MDL but less than the LRL. chromatography/triple quadruple mass spectrometry method Generally, concentrations that are less than the LRL have more to determine the triazole compounds in water (Wisconsin uncertainty in their quantification than concentrations larger State Laboratory of Hygiene, 2007). The method is considered than LRLs. The WSLH data also have been reported with an experimental because it has not received standard approval by “E” remark code. In this case, the “E” remark code indicates the USEPA or other method approving entities. the value is estimated and less than the limit of quantitation, The USGS Reston Chlorofluorocarbon Laboratory in but equal to or greater than the LOD. The limit of quantitation Reston, Virginia, analyzed nine groundwater samples for dis- is the level above which quantitative results may be obtained solved gases (argon, carbon dioxide, methane, nitrogen, and with a specified degree of confidence. The limit of quantitation oxygen) using gas chromatography (Busenberg and others, is defined mathematically as equal to 10 times the standard 2001). Dissolved gas samples were all analyzed in duplicate. deviation of a series of replicate results used to determine the For the purpose of this study, the mean and standard devia- LOD (Wisconsin Department of Natural Resources, 1996). tion have been reported to represent duplicate dissolved Concentrations of the redox-sensitive species of ferrous 2+ gas concentrations. iron (Fe ), sulfide [sum of dihydrogen sulfide (aqueous2 H S), Low-concentration range dissolved oxygen, sulfide, hydrogen sulfide (HS–), and sulfide (S2–)], and dissolved oxy- – 2+ and ferrous iron were analyzed in the field laboratory using gen (O2), along with nitrate (NO3 ), manganese (Mn ), sulfate ® 2– a HACH DR 2800 spectrophotometer (HACH, 2007). (SO4 ), and methane (CH4), were used to assess the biologi- Methods of analyses included HACH® method 8316, which cal redox status using the classification scheme of McMahon is the indigo carmine method using AccuVac ampoules for and Chapelle (2008). Because redox processes in groundwater Methods of Data Collection and Analysis 11 tend to segregate into zones dominated by a single electron- and organic-free blank water was obtained from the NWQL accepting process, the redox framework uses the concentra- and is certified to be free of inorganic and organic constituents. tions of the redox-sensitive species to assign the predominant Trip blanks for this study were VOC vials of laboratory blank redox process to groundwater samples. An automated spread- water, filled and sealed by TestAmerica Laboratories. These sheet program was used to assign the redox classification to trip blanks accompanied environmental sample vials to verify each sample (Jurgens and others, 2009). If a redox assignment that VOC contamination did not take place during storage, was not determined for a sample, it likely is due to missing sampling, or shipment to or from TestAmerica. Three trip data for one or more of the redox-sensitive species. A detailed blanks were analyzed for this study: one trip blank for each description of the redox classification framework is presented round of sampling that included collection of VOC samples. in McMahon and Chapelle (2008) and Chapelle and others A quantified result in any blank sample was considered (2009); spreadsheet instructions and details of redox assign- evidence that contamination could have affected groundwater ments are presented in Jurgens and others (2009). A brief sample results. Analytical results for groundwater samples and description of redox assignments follows. When all five redox- associated replicate samples were compared to the maximum sensitive species are entered, the general redox category (oxic, quantified concentration in any blank collected during the suboxic, anoxic, or mixed) is determined from the redox pro- same sampling event. In accordance with USEPA guidance cess. For samples that have sulfide measurements in addition (U.S. Environmental Protection Agency, 1989, p. 5–17), a to the five redox-sensitive species, Fe3+ and SO 2– reduction is 4 reported concentration in an environmental sample that is less differentiated in the redox processes column using the calculated iron/sulfide ratio. For samples missing one or more of the than five times the concentration in a related blank sample should be qualified. Constituents that have been qualified redox-sensitive species other than O2, samples are reported as “O ≥0.5 mg/L” for dissolved-oxygen concentrations greater according to USEPA guidance are identified by a footnote in 2 the water-quality data tables presented in this report. For data than or equal to 0.5 mg/L or as “O2<0.5 mg/L” for dissolved- oxygen concentrations less than 0.5 mg/L. analysis purposes, these values are considered to be nondetections. All qualifications were based on quantified results in field-equipment blank or trip blank samples. Quality-Control Sample Collection and Data Field-equipment and trip blank sample results for Analysis inorganic and organic constituents are presented in appendix 3. Overall, six compounds (ammonia as nitrogen, phospho- In addition to collection of environmental groundwater rus, manganese, DOC, benzene, and methylene chloride) and surface-water samples, quality-control samples includ- were detected in blank samples resulting in qualification of ing field-equipment blanks, trip blanks, and replicates were groundwater sample results. All of these compounds were collected. Analytical results from quality-control samples col- detected in blank samples at concentrations slightly above lected in the field and prepared in the laboratories were used reporting levels, indicating field and laboratory contamination to assess the quality of the data reported for environmental was minimal. samples. Data from quality-control samples collected during Potential variability was estimated using replicate this study were evaluated to estimate the bias and variability groundwater samples. Replicate groundwater samples were that may have resulted from sample collection, processing, collected immediately after the environmental groundwater and analysis. sample, and were analyzed for the same constituents as the Bias was estimated using two types of blank samples sub- environmental sample to provide a measure of variability mitted to analytical laboratories for analysis: field-equipment blanks and trip blanks. Four field-equipment blanks were which might be due to the effects of field and laboratory pro- collected between samples; that is, after the collection of an cedures. Several replicate samples were collected during 2011 environmental sample and cleaning of the sampling equip- and 2012. One replicate sample was collected and analyzed for ment, and just before the collection of the next environmental a full suite of constituents and two additional replicate samples sample. The field-equipment blank is a measure of sampling were collected and analyzed for triazoles. Additionally, bias, providing data used to determine if cleaning procedures samples for all of the dissolved gases (argon, carbon dioxide, removed constituents from sampling equipment between sites methane, nitrogen, and oxygen) were collected and analyzed and if sampling and laboratory methods were appropriate to in replicate. Variability for each analyte is estimated as the prevent contamination of environmental samples (Mueller relative percent difference (RPD) between constituent concen- and others, 1997). Upon completion of cleaning, the field- trations measured in the primary environmental sample and equipment blank was collected by passing specially prepared the replicate environmental sample. The RPD was calculated blank water through all sampling equipment. Inorganic-free using equation 1.

    concentrationc environmental sample − ooncentration replicate sample RPD = absolute value ×100 (1)  concentration environmental ssample − concentration replicate sample     2  12 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Table 3. Volatile organic compounds, gasoline-range organics, and diesel-range organics analyzed in groundwater and surface-water samples at TestAmerica Laboratories, Inc., laboratory reporting levels, and related U.S. Environmental Protection Agency drinking- water standards and health advisories.

[Compounds detected during study are shown in bold type. USEPA, U.S. Environmental Protection Agency; --, not applicable; DRO, diesel-range organics;

C6–C10 and C10–C36, ranges of carbon compounds included in the analysis; µg/L, micrograms per liter]

USEPA drinking-water Chemical Abstracts Service Laboratory Compound Common name/synonym standard or health (CAS) registry number1 reporting level advisory Volatile organic compounds 1,1-Dichloroethane Ethylidene dichloride 75-34-3 0.50 -- 1,1-Dichloroethene Vinylidene chloride 75-35-4 0.50 27 1,1-Dichloropropene -- 563-58-6 0.50 -- 1,1,1-Trichloroethane Methylchloroform 71-55-6 0.50 2200 1,1,1,2-Tetrachloroethane -- 630-20-6 0.50 3100 1,1,2-Trichloroethane Vinyl trichloride 79-00-5 0.50 25 1,1,2,2-Tetrachloroethane -- 79-34-5 0.50 340 1,2-Dibromo-3-chloropropane DBCP, Nemagon 96-12-8 0.50 20.2 1,2-Dibromoethane Ethylene dibromide (EDB) 106-93-4 0.50 20.05 1,2-Dichlorobenzene o-Dichlorobenzene 95-50-1 0.50 2600 1,2-Dichloroethane Ethylene dichloride 106-06-2 0.50 25 1,2-Dichloropropane Propylene dichloride 78-87-5 0.50 25 1,2,3-Trichlorobenzene -- 87-61-6 0.50 -- 1,2,3-Trichloropropane Allyl trichloride 96-18-4 0.50 44 1,2,4-Trichlorobenzene -- 120-82-1 0.50 270 1,2,4-Trimethylbenzene Pseudocumene 95-63-6 0.50 -- 1,3-Dichlorobenzene m-Dichlorobenzene 541-73-1 0.50 5600 1,3-Dichloropropane Trimethylene dichloride 142-28-9 0.50 -- 1,3,5-Trimethylbenzene Mesitylene 108-67-8 0.50 610,000 1,4-Dichlorobenzene p-Dichlorobenzene 106-46-7 0.50 275 2-Chlorotoluene 1-chloro-2-methylbenzene 95-49-8 0.50 5100 2,2-Dichloropropane -- 594-20-7 0.50 -- 4-Chlorotoluene 1-chloro-4-methylbenzene 106-43-4 0.50 5100 4-Isopropyltoluene 4-Cymene 99-87-6 0.50 -- Benzene Pyobenzol 75-43-2 0.50 25 Bromobenzene Phenyl bromide 108-86-1 0.50 560 Bromochloromethane Methylene chlorobromide 74-97-5 0.50 590 Bromodichloromethane Dichlorobromomethane 75-27-4 0.50 2,780 Bromoform Tribromomethane 75-25-2 0.50 2,780 Bromomethane Methyl bromide 74-83-9 1.0 510 Carbon tetrachloride Tetrachloromethane 56-23-5 0.50 25 Chlorobenzene Monochlorobenzene 108-90-7 0.50 2100 Chloroethane Ethyl chloride 75-00-3 1.0 -- Chloroform Carbon trichloride 67-66-3 0.50 2,780 Chloromethane methyl chloride 74-87-3 0.50 49,000 cis-1,2-Dichloroethene (Z)-1,2-Dichloroethene 156-59-2 0.50 270 cis-1,3-Dichloropropene (Z)-cis-1,3-Dichloropropene 542-75-6 0.50 340 Dibromochloromethane Chlorodibromomethane 124-48-1 0.50 2,780 Methods of Data Collection and Analysis 13

[Compounds detected during study are shown in bold type. USEPA, U.S. Environmental Protection Agency; --, not applicable; DRO, diesel-range organics;

C6–C10 and C10–C36, ranges of carbon compounds included in the analysis; µg/L, micrograms per liter]

USEPA drinking-water Chemical Abstracts Service Laboratory Compound Common name/synonym standard or health (CAS) registry number1 reporting level advisory Dibromomethane Methylene dibromide 74-95-3 0.50 -- Dichlorodifluoromethane CFC-12, Freon 12 75-71-8 0.50 51,000 Ethylbenzene Phenylethane 100-41-4 0.50 2700 Hexachlorobutadiene Perchlorobutadiene 87-68-3 0.50 590 Isopropylbenzene (1-methylethyl)benzene 98-82-8 0.50 84,000 Methylene chloride Dichloromethane 75-09-2 0.50 25 Methyl tert-butyl ether9 MTBE 1634-04-4 0.50 1020–40 Naphthalene11 Naphthene 91-20-3 1.0 5100 n-Butylbenzene 1-Phenylbutane 104-51-8 0.50 -- n-Propylbenzene Isocumene 103-65-1 0.50 -- o-Xylene 1,2-Dimethylbenzene 95-47-6 0.50 2,1210,000 sec-Butylbenzene (1-Methylpropyl)benzene 135-98-8 0.50 -- Styrene Ethenylbenzene 100-42-5 0.50 2100 tert-Butylbenzene (1,1-Dimethylethyl)benzene 98-06-6 0.50 -- tert-Butyl ethyl ether9 Ethyl tert-butyl ether (ETBE) 637-92-3 0.50 -- Tetrachloroethene Perchloroethene (PCE), 127-18-4 0.50 25 tetrachloroehtylene Toluene Methylbenzene 108-88-3 0.50 21,000 trans-1,2-Dichloroethene (E)-1,2-Dichloroethene 156-60-5 0.50 2100 trans-1,3-Dichloropropene (E)-1,3-Dichloropropene 10061-02-6 0.50 -- Trichloroethene TCE, trichloroethylene 79-01-6 0.50 25 Trichlorofluoromethane CFC-11, Freon 11 75-69-4 0.50 52,000 Vinyl chloride Choroethene 75-01-4 0.50 22 Xylene, total Dimethylbenzene 1330-20-7 0.50 2,1210,000 Gasoline-range organics Gasoline-range organics GRO -- 25 --

(C6–C10) Diesel-range organics

DRO, C10–C36 -- -- 0.49–0.55 -- 1This report contains CAS Registry Numbers®, which is a registered trademark of the American Chemical Society. The CAS recommends the verification of the CAS Registry Numbers through CAS Client ServicesSM. 2U.S. Environmental Protection Agency Maximum Contaminant Level (MCL) (U.S. Environmental Protection Agency, 2012). 3U.S. Environmental Protection Agency Risk-Specific Dose at 10-4 Cancer Risk (RSD4) (U.S. Environmental Protection Agency, 2012). 4U.S. Environmental Protection Agency Reference Dose (RfD), daily oral exposure (U.S. Environmental Protection Agency, 2012). 5U.S. Environmental Protection Agency Life-time Health Advisory Level (U.S. Environmental Protection Agency, 2012). 6U.S. Environmental Protection Agency, One-day Health Advisory Level, 10-kilogram child (U.S. Environmental Protection Agency, 2012). 7The total for all trihalomethanes cannot exceed 80 µg/L (U.S. Environmental Protection Agency, 2012). 8U.S. Environmental Protection Agency Drinking Water Equivalent Level (DWEL, lifetime exposure (U.S. Environmental Protection Agency, 2012). 9This compound was analyzed as part of volatile organic compounds analysis but actually is an ether used as a fuel oxygenate. 10The U.S. Environmental Protection Agency Drinking-Water Advisory ranges from 20 to 40 µg/L (U.S. Environmental Protection Agency, 2012). 11Napthalene was analyzed as part of the volatile organic compounds analysis but actually is a semivolatile compound. 12The total for all xylenes combined cannot exceed 10,000 µg/L (U.S. Environmental Protection Agency, 2012). 14 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

RPDs were calculated only for constituents with detections, which for this study included only inorganic constituents, triazoles and dissolved gases. RPDs were not calculated for sample pairs where one value was reported as less than the MRL or LRL and the other value was reported as greater than the MRL or LRL, or was estimated. For this study, RPD values greater than 20 percent were considered indicative that analytical results might be affected by high variability. The RPDs for dissolved gases were all 10 percent or less and are not presented in this report. The RPD results for inorganic constituents and triazoles are presented in table 4. Overall, three constituents (nitrate plus nitrite, iron, and 5-MeBT) were qualified because of high variability. These compounds have been identified with a footnote in the water-quality tables where analytical results are presented. Concentrations of bromide, nitrate plus nitrite as nitrogen, and nitrate as nitrogen in environmental and replicate samples were small, causing small concentration differences to result in large RPDs. Although the variability of iron concentrations was high, the magnitude of measured iron concentrations was still substantial. The accuracy of major-ion analyses was checked by calculating a cation-anion balance. The sum of concentrations of dissolved cations in milliequivalents per liter should equal the sum of concentrations of dissolved anions in milliequivalents per liter (Hem, 1989). The percent difference between the sum of concentrations of cations and anions in milliequivalents per liter was calculated using equation 2:

 sumo fdissolved cations − sumofd issollved anions  Percentd ifference =  ×100 (2)  sumo fdissolved cations + sumofd issolved anionns 

Ionic charge balances were calculated for groundwater samples and the surface-water sample for which major ion data were available. The ionic charge balances ranged from -1.48 to 6.53 percent. An ionic charge balance within plus or minus 5 percent is considered acceptable (Clesceri and others, 1998). One ionic charge balance exceeded 5 percent (well JH–1.5R during April 2012 at 6.53 percent).

Hydrogeology

The study area lies within Jackson Hole, a geological depression, or “structural basin,” formed by a large block of the Earth’s crust that dropped down along a fault at the base of the Teton Range with its hinge point in the highlands to the east (Love and Reed, 1971). Jackson Hole is bounded on the west by the Teton Range, to the south by the Snake River and Hoback Ranges, to the east by the Gros Ventre Range, and to the north-northeast by the Washakie and Absaroka Ranges, which extend north along the eastern boundary of both Grand Teton and Yel- lowstone National Parks (fig. 1). The geology around the study area is complex with strata ranging from Precambrian basement rocks to Quaternary unconsolidated surficial deposits (fig. 3). Hydrogeology 15

Table 4. Replicate data for major ions, nutrients, dissolved organic carbon, trace elements, and triazoles in groundwater samples from wells at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

[RPD, relative percent difference; --, not applicable; <, less than symbol indicates the chemical was not detected and the value following the less than symbol is the laboratory reporting level]

Well name and sample date JH–1.5D, April 5, 2012 JH–2.5, November 3, 2011 JH–3.5, June 9, 2011 Physical property of Environ- Environ- Environ- constituent Replicate Replicate Replicate mental mental mental Value Value RPD Value Value RPD Value Value RPD Major ions and related characteristics (in filtered water), in milligrams per liter Total dissolved solids ------189 177 6.56 Hardness, total ------157 156 0.64 Calcium ------47.6 47.4 0.42 Magnesium ------9.29 9.24 0.54 Potassium ------2.09 2.09 0.00 Sodium ------7.16 7.15 0.14 Alkalinity as calcium ------162 160 1.24 carbonate Bicarbonate ------197 195 1.02 Bromide ------0.018 0.016 11.76 Carbon dioxide ------6.6 6.5 1.53 Chloride ------3.73 3.72 0.27 Fluoride ------0.39 0.39 0.00 Silica, as silicon dioxide ------17.4 17.2 1.16 Sulfate ------8.14 8.14 0.00 Nutrients and dissolved organic carbon, in milligrams per liter Nitrate plus nitrite ------0.04 0.03 28.57 Nitrate ------0.134 0.121 10.20 Nitrate, as nitrogen ------0.03 0.027 10.53 Nitrite (in filtered water) ------0.019 0.018 5.41 Nitrite (in filtered water), as ------0.006 0.006 0.00 nitrogen Orthophosphate ------0.043 0.044 2.30 Orthophosphate, as phos------0.014 0.014 0.00 phorus Phosphorus, total, as phos------10.011 10.009 0.02 phorus Dissolved organic carbon ------0.53 0.56 5.50 Trace elements and triazoles compounds, in micrograms per liter Iron, water (in filtered ------7.1 15.2 72.65 water) Manganese (in filtered ------21.3 22.4 5.03 water) 4-Methyl-1H-benzotriazole 8.1 8.2 1.23 7.8 7.9 1.27 <0.35 <0.35 -- (in unfiltered water) 5-Methyl-1H-benzotriazole 0.4 0.54 29.79 0.72 0.57 23.26 <0.25 <0.25 -- (in unfiltered water) 1Quantified concentration in the environmental sample is less than five times the maximum concentration in a blank sample. 16 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

A 110°50′ 110°45′ CM Qg pC pC Qg Qa 43°40′ Qls Qt Qa CM Moose CM Qa pC CM Phelps Lake Qg Qg River Qls Tte Qa Snake Qls Qa pC Qa

CM pC ? 191 Qg

89 Qg Granite Creek Qa Qt Qg Qls 26 Jackson Qg pC Hole Airport Qa Qa Qls Qt CM Teton Fault Teton Village Creek 43°35′ A Qg A′ Qls Tte Qg River pC Qa Qg West Ventre Tte Creek Gros Ventre Gros Butte East Qa Tte ? Lake PPM Gros Ventre PPM CM Butte

Moose–Wilson Road Jst

CM PPM QTc Qls QTc CM Qa PPM Aspens Qa QTc CM Fish Creek Qg River Qa ? Qg Qg PPM Jst PPM Qg Qa ? Tii PPM ? PPM 43°30′ Wilson 22 ? Qg Creek CM Qa Qg Qa CM CM Qa Snake Qa PPM Qa QTc QTc Jackson Qg Qg QTc PPM PPM Tii Qt CM CM Cache Kb Flat Qls QTc Qg Kb PPM Qa Spring CM Qg Creek Qg PPM cd Ka Qa PPM ? QTc CM Qg CM Qa Qt 191 cd Qg 89 Qg QTc 26 Qls CM

Base from Wyoming Gap Analysis digital data, 1996, 0 2 4 MILES Geology modified from Case and others, 1998; 1:100,000 Love and Christiansen, 1985; Love and others, Albers Equal-area Conic projection 0 2 4 KILOMETERS 1992; and Love and others, 2003 Standard parallels 41°N and 45°N, central meridian 110°30′W Figure 3. A, Generalized geology and B, geologic section in the vicinity of the Jackson Hole Airport, Jackson, Wyoming (modified from Wright, 2010). Hydrogeology 17

EXPLANATION

Quaternary unconsolidated deposits Mesozoic and Paleozoic rocks Qa Alluvium and colluvium Kb Bacon Ridge Sandstone

Qt Gravel, pediment, and alluvial fan deposits Ka Aspen Shale

Qg Gravel, pediment, talus, and alluvial fan deposits— Jst Stump Formation May include some glacial deposits (fill and outwash) and Tertiary gravels cd Chugwater and Dinwoody Formations

QTc Conglomerate PPM Phosphoria Formation, Wells Formation, Tensleep Jackson Hole (Pleistocene or Pliocene) Sandstone, and Amsden Formation

Qls Landslide deposits CM Flathead Sandstone, Gros Ventre Formation, Gallatin Limestone, Bighorn Dolomite, Darby Formation, and Tertiary sedimentary and igneous rocks Madison Limestone Tte Teewinot Formation Precambrian rocks Granitic and basaltic rocks, granite gneiss, metasedimentary Intrusive and extrusive igneous rocks pC Tii and metavolcanic rocks, metamorphosed mafic and ultramafic rocks

? Fault—Dashed where concealed or approximately located. Bar and ball on downthrown side

Thrust fault (concealed)—Saw teeth on upper plate

Relative fault movement

A A′ FEET 10,000

Qls Teton Fault Teton Gros Ventre River Ventre Gros Teton fault zone branch (?) Teton Fish Creek Snake River Qa, Qt, and Qg 5,000 cd

PPM CM Tte

pC NGVD 29

pC ?

–5,000 0 2 4 MILES

0 2 4 KILOMETERS VERTICAL EXAGGERATION APPROXIMATELY ×2

Details of fault and buried strata are approximate and largely diagrammatic. For simplicity, Quaternary deposits are not distinguished in the geologic section. Schematic based on a nearby cross section in Love and others (2003).

Figure 3. A, Generalized geology and B, geologic section in the vicinity of the Jackson Hole Airport, Jackson, Wyoming (modified from Wright, 2010).—Continued 18 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Surficial deposits in the vicinity of the JHA consist of relatively uniform, in spite of regular pumping of production unconsolidated Quaternary gravel, pediment, and fan deposits, wells in the study area. whereas surficial deposits at the airport are predominantly ter- Monitor wells JH–1.5(JH–1.5R) and JH–1.5D composing race gravels underlain by siltstone deposits of the Chugwater well cluster 1.5 and wells JH–3 and JH–3D composing well and Dinwoody Formations (fig. 3) (Love and others, 2003). cluster 3 were located adjacent to each other and completed at Lithologic logs of wells installed for this study indicate the different depths in part to evaluate the hydraulic potential (dif- Quaternary deposits range in size from sand to cobble with ferences in hydraulic head or groundwater level) for vertical most deposits primarily consisting of coarse gravel (Jack groundwater flow at the location. The vertical gradient in the Weber, Weber Well Drilling, written commun., 2009). Snake River alluvial aquifer at both well clusters was small. Water levels in unconfined aquifers like the Snake River Calculations of the vertical hydraulic gradient at well clus- alluvial aquifer commonly vary seasonally. Graphical repre- ter 1.5 varied throughout the period of record, ranging from sentations of water levels (hydrographs) measured throughout -0.011 ft/ft in May 2011 to 0.021 ft/ft in August of 2011 when the baseline and followup studies are presented in figure 4 the gradient changed from negative to positive. An increas- for wells JH–1, JH–2, JH–3 and JH–4. Discrete water levels ing water-level altitude with depth (appendix 2) indicates a for all monitoring wells also are presented in figure 4. For the hydraulic potential for upward groundwater flow, whereas a baseline study, Wright (2010) documented that the water-level decreasing water-level altitude with depth (appendix 2) indi- surface of the Snake River alluvial aquifer varied seasonally, cates a hydraulic potential for downward groundwater flow. It reflecting a pattern affected by precipitation-driven recharge is not clear why there was a change in the vertical gradient at (primarily snowmelt) during April–June and irrigation-induced well cluster 1.5. Calculations of the vertical hydraulic gradi- recharge during June–October, with minimal aquifer recharge ent at well cluster 3 indicated this gradient varied throughout during November–March. The hydrographs displayed in the year, ranging from a low of 0.0004 ft/ft in June 2011 to a figure 4 indicate that water levels in the Snake River alluvial high of 0.009 ft/ft in April 2012, with an average of 0.005 ft/ft. aquifer continued to vary seasonally during the followup The vertical gradient at well cluster 3 consistently indicates study, reflecting the precipitation-driven recharge pattern a hydraulic potential for downward groundwater flow in the described above. Although the actual high and low points of Snake River alluvial aquifer at this location, consistent with the water table vary from year to year, the water table was at previous results (Wright, 2010). The ratio of the average hori- its lowest level in late March to early April, at the beginning zontal hydraulic gradient to the average vertical hydraulic gra- of spring, and at its highest level in July to August at the end dient at well cluster 3 is 1.36. Meaning that for every 1.36 ft of the peak of snowmelt. The water level increased about 12.5 that water moves horizontally, water also is likely to move to 15.5 ft between April and July 2011 and about 8 to 10 ft 1 ft vertically (downward), assuming horizontal and vertical between April and July 2012 (fig. 4). Well JH–1 consistently conductivities of aquifer materials are the same. had the highest water-level altitudes, and well JH–2 had the Horizontal groundwater velocities were calculated for lowest water-level altitudes (appendix 2, fig. 4). On average, each airport visit using hydraulic conductivity values from the water-table altitude between wells JH–1 and JH–2 (a dis- both Teton Village and the Aspens (table 6) and an estimated tance of about 3,542 ft) dropped a little more than 22 ft. porosity as described previously in the “Methods of Data Water-table contours were drawn (figs. 5A–B) using both Collection and Analysis” section. Groundwater velocity was discrete water-level measurements and contours determined estimated as high as 68 foot/day (ft/d) using average hydrau- using multiple three-point calculations to assist with “fitting” lic gradients calculated for July and November 2011 and of contours. A water-table contour map was constructed for April 2012, and the hydraulic conductivity for Teton Village; two water-level measurement events: low water table in April the groundwater velocity was estimated to be as low as 25 ft/d 2012 (fig. 5A) and high water table in July 2012 (fig. B5 ). using the average hydraulic gradient calculated for May 2011 The direction of groundwater flow generally is to the west- and the hydraulic conductivity for the Aspens (table 6). The southwest, assuming groundwater flow is perpendicular to range of hydraulic gradients determined during 2011 and 2012 water-table contours. The direction of groundwater flow has is slightly broader than the hydraulic gradients for the period not changed substantially since 2009 (Wright, 2010). Seasonal of 2008 and 2009 (Wright, 2010). The change in horizontal variations in the direction of groundwater flow appear to be hydraulic conductivity values between the 2008––09 and minimal. Horizontal hydraulic gradients were calculated for 2011–12 studies could be due to variations in the local climate. several combinations of monitoring wells for the period of Using an estimated linear distance of 3,540 ft from well JH–1 May 2011 to July 2012 and are presented in table 5. Horizon- to well JH–2, it would take approximately 52 to 142 days for tal hydraulic gradients ranged from 0.0062 foot per foot (ft/ft) water in the aquifer to travel from well JH–1 (upgradient from to 0.0072 ft/ft, with an average of 0.0068 ft/ft (table 5), which airport operations) to the southwest boundary of the airport. is slightly higher than the average of 0.0066 ft/ft determined The calculated rates of horizontal groundwater velocity during the baseline study (Wright, 2010). The spatial unifor- (table 6) are estimates and could vary at different locations at mity of calculated hydraulic gradients across the airport indi- the JHA. Although lithologic data for monitoring wells JH–1 cates that the hydraulic gradient of the aquifer at the airport is through JH–4, coupled with a fairly narrow range of hydraulic Hydrogeology 19

6,390

6,380

6,370

6,360 Altitude of water level, in feet above North American Vertical Datum of 1988 Altitude of water level, in feet above North American Vertical

6,350 2

1.5

0.5

0 Precipitation, in inches SOND JFMAMJJASOND JFMAMJJASOND JFMAMJJASOND JFMAMJJAS 2008 2009 2010 2011 2012 Year and month

EXPLANATION Transducer data, unit values Well JH–1 Well JH–2 Well JH–3 Well JH–4 Discrete water-level measurement Well JH–1 Well JH–1.5 Well JH–1.5R Well JH–1.5D Well JH–2 Well JH–2.5 Well JH–3 Well JH–3D Well JH–3.5 Well JH–4

Figure 4. Water levels for selected wells sampled at the Jackson Hole Airport, Jackson, Wyoming with precipitation data collected at Moose, Wyoming, station 486428 (High Plains Regional Climate Center, 2013), water years 2008–12. 20 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

A Control tower 6,369.38

6,380 N

Spring Gulch Road

6,375 Teton Interagency Helitack Crew operations center

JH–1 6,377.57

JH–4 6,360.62 Terminal

Airport 6,370 parking E. Trap Club Rd.

Direction of6,365 groundwater flow North hangar Hangar 1 Fuel farm JH–1.5 (no water Hangar 2 6,372.04 JH–3.5 level collected) Airport entrance 6,356.21 6,373.53 JH–1.5R 6,360.64 Ea Middle st JH–3 hangar Air JH–1.5D port 6,357.71 6,360.31 Road Hangar 3 Leach field JH–3D 6,370.54 South Side Septic tanks 6,357.33 6,360 fuel farm 6,371.66 Rental car buildings JH–2.5 Leach field Ponderosa Dr. 6,359.46 Auto garage Septic tank South hangar 6,368.07

Spring Gulch Road

Jackson Hole Aviation rotate hangar Hangar 5 6,367.34 Hangar

Irrigation ditch

JH–2 Ponderosa Dr. 6,354.43

6,355

EXPLANATION 6,355 Water-table contour—Shows altitude of water table in feet above North American Vertical Datum of 1988 (NAVD 88). Dashed where approximately located. Contour interval 5 feet Hangar 5 Well where groundwater level was measured and identifier— 6,367.34 0 500 1,000 FEET Number in blue is altitude of water level in feet above NAVD 88 JH–2 Well where groundwater level was measured and water-quality 0 150 300 METERS 6,354.43 samples were collected and identifier—Number in blue is altitude of water level in feet above NAVD 88

Control tower B 6,376.31

Spring Gulch Road

Teton Interagency Helitack Crew operations center

JH–1 6,385.37

JH–4 Terminal 6,368.61 Airport 6,380 parking

E. Trap Club Rd.

North Hangar 1 Direction of groundwater flowhangar Fuel farm JH–3.5 Hangar 2 Airport entrance 6,365.43 JH–1.5 6,369.02 6,375 6,380.06 6,381.71 JH–1.5R 6,369.02 E ast JH–1.5D Middle hangar Air JH–3 port Road 6,369.02 6,366.28 Hangar 3 Leach field JH–3D 6,378.62 Septic tanks 6,366.04 6,370 South Side fuel farm 6,379.71 Rental car buildings JH–2.5 Auto garage Ponderosa Dr. 6,368.28 6,376.41 Leach field Septic South hangar tank

Spring Gulch Road

Jackson Hole Aviation rotate Hangar 5 hangar 6,375.73 Hangar

Irrigation ditch

Ponderosa Dr. JH–2 6,364.13 6,365 EXPLANATION 6,365 Water-table contour—Shows altitude of water table in feet above North American Vertical Datum of 1988 (NAVD 88). Dashed where approximately located. Contour interval 5 feet Hangar 5 Well where groundwater level was measured and identifier— 6,375.73 0 500 1,000 FEET Number in blue is altitude of water level in feet above NAVD 88 JH–2 Well where groundwater level was measured and water-quality 0 150 300 METERS 6,364.13 samples were collected and identifier—Number in blue is altitude of water level in feet above NAVD 88

Figure 5. Water-table contours and estimated direction of groundwater flow in A, low water table in April 2012; and B, high water table in July 2012, Jackson Hole Airport, Jackson, Wyoming.—Continued 22 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming gradients for these wells, indicate the Snake River alluvial Groundwater velocity estimates (table 6) only describe aquifer at the airport is relatively homogeneous, horizontal movement of groundwater in the Snake River alluvial aquifer hydraulic conductivity differs from point to point and along and are not applicable to solute movement. Solute movement a flow path because lithology typically is heterogeneous and through saturated media, such as an aquifer, is affected by anisotropic. The actual groundwater velocity may be differ- advection as well as other physical processes such as diffusion ent between two points depending on the heterogeneity of the and dispersion, and chemical processes such as sorption, pre- aquifer. The direction of flow also might not be perpendicular cipitation, oxidation and reduction, and biodegradation (Fetter, to water-table contours as shown in figures 5 A–B (due to 1993). Consequently, some solutes may move at a rate much anisotropy) and likely is not in a straight line. These factors, different than groundwater flow through the aquifer. and the estimated porosity value chosen, could substantially affect the groundwater velocity estimates.

Table 5. Horizontal hydraulic gradients calculated for selected water-level measurement events at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

Wells used in three-point Horizontal hydraulic gradient (foot per foot) calculation to determine hydraulic gradient May 2011 July 2011 November 2011 April 2012 July 2012 Average JH–1, JH–2, JH–4 0.0062 0.0069 0.0070 0.0069 0.0066 0.0067 JH–1, JH–3, JH–4 0.0064 0.0070 0.0069 0.0071 0.0067 0.0068 JH–1, JH–2, JH–3 0.0063 0.0072 0.0071 0.0070 0.0068 0.0069 Average by month 0.0063 0.0070 0.0070 0.0070 0.0067 0.0068

Table 6. Results of groundwater-velocity calculations using hydraulic conductivity values of the Snake River alluvial aquifer at Teton Village and the Aspens.

[K, hydraulic conductivity; ft/d, feet per day; dh, change in head; dl, change in distance; ft/ft, foot per foot; n, porosity; ft/d, feet per day]

Horizontal hydraulic Average hydraulic Porosity from Heath, 1983 Velocity estimate Date conductivity (K) gradient (dh/dl) (n) (percent) (ft/d) (ft/d) (ft/ft) Hydraulic conductivity at Teton Village (Nelson Engineering, 1992) May 2011 2,900 0.0063 0.3 61 July 2011 2,900 0.0070 0.3 68 November 2011 2,900 0.0070 0.3 68 April 2012 2,900 0.0070 0.3 68 July 2012 2,900 0.0067 0.3 65 Average 2011–2012 2,900 0.0068 0.3 66 Hydraulic conductivity at the Aspens (Nelson Engineering, 1992) May 2011 1,200 0.0063 0.3 25 July 2011 1,200 0.0070 0.3 28 November 2011 1,200 0.0070 0.3 28 April 2012 1,200 0.0070 0.3 28 July 2012 1,200 0.0067 0.3 27 Average 2011–2012 1,200 0.0068 0.3 27 Water Quality 23

Water Quality (µS/cm) (table 7, appendix 4). These values were similar to the range of values for dissolved solids (91 to 538 mg/L) and Constituent concentrations in samples collected for the specific conductance (112 to 863 µS/cm) reported by Nolan followup study are compared to the USEPA drinking-water and Miller (1995) for water from wells producing from Qua- standards and health advisories for drinking water (U.S. ternary alluvium, colluvium, and gravel, and pediment, fan, Environmental Protection Agency, 2012) listed in tables 3 and glacial deposits in Teton County, Wyoming. Calculated and 7. Although none of the wells sampled for this study hardness concentrations ranged from 120 to 310 mg/L (as CaCO ), making water at the airport generally moderately hard are used to supply drinking water, USEPA drinking-water 3 (61 to 120 mg/L as CaCO ) to very hard (121 to 180 mg/L as standards and health advisories provide a basis for assessing 3 CaCO ) (Hem, 1989). the groundwater quality at the JHA. No constituents were 3 detected at concentrations exceeding the USEPA Maximum The major ion composition of groundwater in the study Contaminant Levels (MCLs) or health advisories; how- area largely results from chemical reactions between water and ever, concentrations for some constituents exceeded USEPA sediments in the soil and aquifer and, to a lesser extent, from Secondary Maximum Contaminant Levels (SMCLs). The ions in precipitation. The relative proportions of the major SMCLs are non-enforceable standards for constituents that cations (calcium, magnesium, potassium, and sodium) and may cause cosmetic effects (discoloration of teeth or skin) or the major anions [bicarbonate plus carbonate (based on field aesthetic effects (undesirable taste, odor, or color) in drinking titration), chloride, fluoride, and sulfate] were used to describe water (U.S. Environmental Protection Agency, 2012). Redox the water type at each well. The average ion composition for measurements indicate oxygen-poor conditions in many of samples from each well was plotted on a trilinear diagram the wells. Many anthropogenic constituents were included in (fig. 6). The sample compositions presented in figure 6 are sample analyses, and six of these constituents, including one differentiated by the study (baseline or followup) for which GRO, three VOCs, and two triazole compounds, were detected they were collected. The triangles on the bottom left and right (many at qualified concentrations) in groundwater samples. show the relative percentages of cations and anions, whereas Results from analyses of groundwater samples collected the quadrangle in the center is a combination of all the ion data during this study are summarized in tables 3 and 7, and are (Piper, 1944). There was little to no difference between the ion presented in detail in appendixes 4, 5, 6, 7, and 8. Results composition of samples collected for the baseline study and from analyses of the surface-water sample collected from the followup study. As reported in Wright (2010), calcium was irrigation ditch are presented in appendixes 4, 5, 7, and 8. No the dominant cation, and bicarbonate was the dominant anion; VOCs, DROs, GROs, or triazoles were detected in the surface- thus, the water type for all the wells sampled at the airport was water sample; thus, only the groundwater-quality findings at calcium bicarbonate (fig. 6). the JHA for water years 2011 and 2012 are described further in this section. Redox Conditions Chemical Composition The chemical quality of groundwater commonly is affected by redox processes (Chapelle and others, 2009). Dur- Natural waters, such as groundwater, contain a wide ing the 2008–09 baseline study, Wright (2010) reported that variety of dissolved substances. These dissolved substances most groundwater measured at the JHA was oxic (oxygen- are derived from many sources, a few of which include ated), whereas groundwater from two wells (JH–3 and JH–3D) atmospheric gases, weathering and erosion of rocks and soils was reduced (oxygen-poor). Reduction reactions generally are the water has contacted, solution and precipitation of miner- sequential and happen in a specific order as long as reac- als, and biochemical processes (Hem, 1989). Many common tants are available. The sequence starts with the reduction of physical and chemical properties were measured during this oxygen and progresses through nitrate reduction, reduction of study. These properties are summarized in table 7 with all manganese oxides, reduction of iron oxides, sulfate reduc- physical property data presented in appendix 4. The properties tion, and finally methanogenesis (Appelo and Postma, 2005; that best describe the groundwater composition in the Snake McMahon and Chapelle, 2008). Each of these reactions either River alluvial aquifer are described further in this section of causes the disappearance of a reactant or the appearance of the report. a reaction product, changing the groundwater composition. Groundwater was neutral to alkaline (pH values ranged This section presents results for dissolved oxygen, nutrients, from 7.0 to 8.0) with concentrations of alkalinity as calcium trace elements, dissolved gases, DOC, and COD in an effort carbonate (CaCO3) ranging from 112 to 328 mg/L. Ground- to highlight the effect reducing conditions have had on the water at the airport was fresh (dissolved solids concentration groundwater composition at the previously described wells. less than 1,000 mg/L; Heath, 1983), with dissolved solids The dissolved-oxygen concentration was measured each concentrations ranging from 150 to 382 mg/L (appendix 5). time a well was sampled and was the first indication of the Specific-conductance values were low, ranging from 247 redox condition of water in each well. Dissolved-oxygen con- to 622 microsiemens per centimeter at 25 degrees Celsius centrations measured using a field meter ranged from <0.1 to 24 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Table 7. Summary of physical properties and inorganic groundwater-quality data collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

[mg/L, milligrams per liter; µS/cm, microsiemens per centimeter at 25 degrees Celsius; °C, degrees Celsius; NTRU, nephelometric turbidity ratio units; CaCO3, calcium carbonate; HCO3, bicarbonate; SiO2, silica; N, nitrogen; n, below the lower reporting level and above the long term method detection level; b, value extrapolated at low end; <, less than; USEPA, U.S. Environmental Protection Agency; --, not applicable; SMCL, Secondary Maximum Contaminant Level; DWA, Drinking Water Advisory; MCL, Maximum Contaminat Level; HAL, Health Advisory Level]

CaCO3, calculated Calcium 25/25 35.2 57.3 96 -- -- Magnesium 25/25 7.41 10.50 17.10 -- -- Potassium 25/25 1.79 2.04 2.61 -- -- Sodium 25/25 6.43 7.63 8.35 420 (DWA), 0 530–60 (DWA) Alkalinity, field, as 35/35 112 178.9 328 -- --

CaCO3

Bicarbonate, as HCO3 35/35 130 217.6 400 -- -- Chloride 25/25 3.19 5.48 13.10 2250 (SMCL) 0 Fluoride 25/25 0.32 0.39 0.48 34 (MCL), 0 22 (SMCL)

Silica as SiO2 25/25 17.4 20.1 23.7 -- Sulfate 25/25 0.16 6.54 11.6 2250 (SMCL), 0 4500 (DWA) Nutrients, in milligrams per liter, dissolved (samplefiltered through 0.45-micrometer filter) Ammonia as nitrogen 10/22 n0.011 0.05 0.294 630 (HAL) 0 Nitrate plus nitrite as 9/22 bn0.02 0.32 1.35 310 (MCL) 0 nitrogen Nitrite as nitrogen 5/22 bn0.002 0.01 0.007 31 (MCL) 0 Total nitrogen (nitrate 7/22 0.14 0.56 1.47 -- -- plus nitrite plus ammonia plus organic- N), unfiltered Orthophosphate as 22/22 n0.006 0.02 0.055 -- -- phosphorus Phosphorus, as phos- 22/22 n0.006 0.02 0.111 -- -- phorus Water Quality 25

Table 7. Summary of physical properties and inorganic groundwater-quality data collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.—Continued

Number of USEPA Number of detec- Minimum Median Maximum value USEPA drinking- drinking-water Constituent or physical tions/number of value or value or or water standards1, 2 or standard or characteristic samples concentration concentration concentration health advisories3, 4, 5, 6 health advisory exceedances Trace elements, in micrograms per liter unless otherwise noted, dissolved (sample filtered through 0.45-micrometer filter) Bromide (mg/L) 24/25 bn0.012 0.02 0.041 -- -- Iron 26/35 n3.4 368 1,050 2300 (SMCL) 13 Manganese 27/35 n0.18 887.5 3,040 250 (SMCL) 21 Other analyses (dissolved organic carbon sample filtered through 0.45-micrometer filter) Chemical oxygen 0/20 <10 <10 <10 -- -- demand Dissolved organic 20/20 bn0.36 1 4.12 -- -- carbon 1Median values were determined using detections and nondetections. 2U.S. Environmental Protection Agency Secondary Maximum Contaminant Level (SMCL) (U.S. Environmental Protection Agency, 2012). 3U.S. Environmental Protection Agency Maximum Contaminant Level (MCL) (U.S. Environmental Protection Agency, 2012). 4The U.S. Environmental Protection Agency Drinking-Water Advisory Health-based Value (U.S. Environmental Protection Agency, 2012). 5The U.S. Environmental Protection Agency Drinking-Water Advisory Taste Threshold (U.S. Environmental Protection Agency, 2012). 6U.S. Environmental Protection Agency Lifetime Health Advisory (HAL) (U.S. Environmental Protection Agency, 2012).

9.0 mg/L (table 7, appendix 4). The dissolved-oxygen mea- were measured in water from wells with dissolved-oxygen surement of 9.0 mg/L, that was collected at well JH–1 on June concentrations less than 1 mg/L using spectrophotometry 8, 2011, is considered questionable because this measurement (appendix 5). This low-level method consistently reported was about 1 mg/L higher than all of the other measurements slightly lower concentrations of dissolved oxygen than the collected from this well (including those from the baseline field meter. study reported in Wright, 2010). This dissolved-oxygen mea- Nutrients were detected at low concentrations in all surement was not used to compute any statistics; however, this 35 groundwater (appendix 5) samples, and all concentrations measurement is presented in appendix 4 because it shows that were less than applicable USEPA MCLs and health advisories the groundwater at well JH–1 during June 2011 was oxygen- (table 7); however, 5 ammonia and 14 phosphorus concentra- ated. Median dissolved-oxygen ranges are presented for each tions were measured at concentrations less than five times monitor well (data for wells JH–1.5 and JH–1.5R have been the maximum quantified concentration measured in blank combined and presented as if they are from one well) in figure samples. In accordance with USEPA guidance (U.S. Envi- 7 based on data collected for followup study (water years ronmental Protection Agency, 1989, p. 5–17), these concen- 2011 and 2012). This map shows the distribution of dissolved- trations were qualified and were footnoted in appendix 5. oxygen concentrations across the JHA. Dissolved-oxygen Total nitrogen was detected in all of the samples except those concentrations indicative of reducing (anoxic or anaerobic) from wells JH–1.5, JH–1.5R, JH–1.5D, JH–3D, and JH–3.5. conditions (a dissolved-oxygen concentration of less than Dissolved nitrate plus nitrite as nitrogen (referred to as 1 mg/L was considered indicative of reducing conditions for nitrate in this report) was detected in samples from all wells this study) were measured in water from 7 of the 10 monitor except wells JH–1.5R, JH–1.5D, JH–3, and JH–3D, indicat- wells sampled (fig. 7). Dissolved-oxygen concentrations in ing nitrate was the primary nitrogen species in the alluvial oxic water from the other wells generally averaged greater aquifer. Ammonia as nitrogen was detected in at least one than 7.0 mg/L in all the wells except JH–2, which had concen- sample from each of the wells (including qualified concentra- trations ranging from a high of 6.9 mg/L in May 2009 (Wright, tions) except well JH–2. Nitrate can be reduced by bacteria to 2010) to a low of 3.3 mg/L in November 2011. In addition nitrous oxide, ammonia, and nitrogen gas (Hem, 1989) when to field measurements, dissolved-oxygen concentrations also exposed to anaerobic conditions; therefore, the presence of 26 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Figure 6. Trilinear diagram showing proportional mean major- 100 EXPLANATION ) ion composition, by study, for groundwater samples collected 4 100 Calcium (Ca) + magnesium (Mg) Groundwater sample from wells at the Jackson Hole Airport, Jackson, Wyoming, 80 ) Baseline study (Wright, 2010) 3 water years 2008–12. 80 Followup study (2011–12) +NO 2 60

60 40

40 20 + nitrite+nitrate (NO

20 Chloride (Cl) + fluoride (F) + sulfate (SO 0 PERCENT

0 0

PERCENT 0

20 0

Sodium (Na) 20 + potassium (K) ) 0 3 100 40 100 20

40 Sulfate (SO 20 80 60 80 40

60 40 ) + carbonate (CO 60 80 3 60 60 4 )

Magnesium (Mg) 80 60 40 100 40 80

80 100 20 Bicarbonate 100 (HCO 20

0 100 80 60 40 20 0 100 0

0 20 40 60 80 100 Calcium (Ca) Chloride (Cl), fluoride (F), and nitrite+nitrate (NO2+NO3) CATIONS ANIONS Percentage of total milliequivalents per liter

ammonia instead of nitrate is another indicator of reducing The dissolved trace elements of iron and manganese were conditions at and in the vicinity of wells JH–3 and JH–3D. detected in at least one sample from all 10 wells and in 27 of One sample collected from well JH–2 during June 2011 had the 35 samples collected during water years 2011 and 2012 higher concentrations of nitrate (1.35 mg/L) and total nitrogen (appendix 5). Three manganese concentrations were measured (1.47 mg/L) than were detected in samples from other airport at less than five times the maximum concentration measured wells. These higher concentrations could be a result of this in blank samples and have been footnoted in appendix 5. well being directly downgradient from the septic leach field The distribution of median dissolved iron and dissolved- at the airport (fig. B5 ), as was reported by Wright (2010) for manganese concentration ranges across the JHA is shown in similar high nitrate concentrations measured in the same well. figure 7. Concentrations of dissolved iron and manganese were These higher observed nitrate concentrations are only slightly less than or near the LRLs (3.2 and 0.16 µg/L, respectively) greater than the median concentration (0.69 mg/L as nitrogen) in samples from three wells (fig. 7). Samples from the remaining seven wells had high concentrations of dissolved iron and reported for nitrite plus nitrate in groundwater samples from manganese (fig. 7); these high concentrations measured in Quaternary deposits within Teton County, Wyoming (Nolan groundwater are an additional indicator of reducing conditions and Miller, 1995), and fall within the range of concentrations (McMahon and Chapelle, 2008). (0 to 2 mg/L) that can be expected in the absence of human Dissolved iron concentrations exceeded the USEPA effects (Mueller and Helsel, 1996). Total phosphorus and dis- SMCL of 300 µg/L (U.S. Environmental Protection Agency, solved orthophosphate (as phosphorus) were detected in water 2012) in 1 of 2 samples from well JH–1.5, in all 4 samples from all 10 wells (table 7; appendix 5). The median value for from well JH–1.5D, in 3 of 4 samples from well JH–3, in all total phosphorus (0.02 mg/L) was slightly greater than the 4 samples from well JH–3D, and in 1 of 3 samples from well median value (0.010 mg/L) reported for total phosphorus in JH–3.5 (fig. 7; table 7; appendix 5). There is some uncertainty groundwater samples from Quaternary deposits within Teton in the reproducibility of iron concentrations because of high County, Wyoming (Nolan and Miller, 1995), and was within RPDs (table 4); however, iron concentrations adjusted for vari- the range (0 to 0.1 mg/L total phosphorus) of concentrations ability would still exceed the SMCL. that Mueller and Helsel (1996) reported could be expected in Dissolved manganese concentrations exceeded the SMCL groundwater in the absence of human effects. of 50 µg/L (U.S. Environmental Protection Agency, 2012) Water Quality 27

EXPLANATION Control tower Fence Hangar 5 Well where groundwater level was measured and identifier JH–2 Well where groundwater level was measured and water-quality samples N were collected and identifier Median constituent concentration (mg/L, milligrams per liter; µS/cm, microsiemens per centimeter at 25 degrees Celsius; µg/L, micrograms per liter) Dissolved Specific Iron, Manganese, 4-Methyl-1H- oxygen conductance, dissolved dissolved benzotriazole, (mg/L) (µS/cm) (µg/L) (µg/L) (µg/L) Less than 0.5 Less than 300 Less than 3.2 Less than 0.16 Less than 0.35 0.5 to 5 300 to 350 3.2 to 30 0.16 to 50 0.35 to 3.5 >5.0 >350 to 400 >30 to 300 >50 to 500 >3.5 to 5.0

Spring Gulch Road >400 >300 >500 >5.0

Teton Interagency Helitack Crew operations center JH–1

JH–4

Terminal

Airport parking

E. Trap Club Rd.

North hangar Hangar 1

Spring Gulch Road Auto garage

Hangar 4 Jackson Hole Aviation rotate hangar Hangar 5 Hangar

Irrigation ditch

Ponderosa Dr. JH–2

0 500 1,000 FEET

0 150 300 METERS

Figure 7. Distribution ranges of median concentrations of selected constituents measured in groundwater samples from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012. 28 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming in several samples from wells JH–2.5 and JH–3.5, and in all Three DOC concentrations were qualified with a footnote in samples collected from wells JH–1.5, JH–1.5R, JH–-1.5D, appendix 5 owing to being measured at less than five times JH–3, and JH–3D (fig. 7; table 7; appendix 5). None of the the maximum concentration measured in a blank sample. The wells sampled for this study are used to supply drinking water. highest concentrations of DOC were measured in samples Samples for analyses of dissolved gases (argon, carbon collected in July 2011 from wells JH–1.5 and JH–1.5D, and in dioxide, methane, nitrogen, and oxygen) were collected from samples collected on July 20, 2011, and April 4, 2012, from all nine existing monitoring wells during June 2011. Dis- well JH–3 (appendix 5); these high DOC concentrations are solved gas measurements are useful for the determination consistent with the determination of reducing conditions in of geochemical reactions along a flow path. Some dissolved those wells. The DOC concentrations in samples collected gases can allow for the determination of recharge areas and during 2011 and 2012, from all 10 wells, were within the the seasonal period that the sample entered the aquifer; others estimated range of 0 to about 3 mg/L considered natural in are helpful when identifying biochemical reactions such as groundwater (Drever, 1997, fig. 6–1), with the exception of the methanogenesis and denitrification. maximum concentration of 4.12 mg/L at well JH–1.5, which For the purpose of this study, the dissolved gas data was only slightly greater. Chemical oxygen demand (COD) provided an additional confirmation of reducing conditions was not detected in samples at concentrations greater than the at many of the wells. The concentrations of dissolved oxygen MRL of 10 mg/L (appendix 5). detected in the dissolved gas samples were used to confirm low field readings and often were lower (appendix 6) than those measured using the field meter (appendix 4). Addition- Anthropogenic Compounds ally, methane gas (appendix 6) was detected in samples from wells with reducing conditions such as well JH–1.5 and not in As a commercial airport, the JHA uses many differ- oxygenated wells such as JH–2 (appendix 6). Methane gas is ent anthropogenic compounds as part of daily operations. produced by methanogenic microorganisms under anaerobic Wright (2010) reported only DRO were detected in measur- conditions (U.S. Geological Survey, 2009). These methano- able quantities during the baseline water-quality study. Only genic conditions generally are present after all the other pos- samples from the new monitor wells were analyzed for VOCs sible “reduction reactants” have been consumed and indicate and GROs, whereas samples from all wells were analyzed for extremely reducing conditions. DROs during the followup study during water years 2011–12. 2+ Ferrous iron (Fe ), hydrogen sulfide (H2S) measured as Data for VOCs, GROs, and DROs for the followup study are 2– sulfide (S ), and a more accurate quantification of low-level presented in appendix 7. dissolved oxygen were analyzed in the field at wells with Samples for analyses of VOCs and GROs were collected measured dissolved-oxygen concentrations less than 1 mg/L. from the five new monitoring wells during June and July 2011 These analyses are presented in table 8 along with the redox and April 2012. Concentrations of GROs were less than the classification assigned to each sample by the automated LRLs used for this study in all except one sample collected spreadsheet program presented in Jurgens and others (2009). from well JH–1.5 on July 20, 2011, which had an estimated Manganese reduction was the dominant process taking place concentration of 11 micrograms per liter (µg/L) (appendix 7). (table 8) at well JH–1.5 during June of 2011 and well JH–2.5 Three of the 63 VOCs included in the analyses (benzene, during June and July 2011. Samples from wells JH–1.5R, ethylbenzene, and total xylene) were detected at small (esti- JH–1.5D, JH–3, and JH–3D had iron-to-sulfide ratios greater mated) concentrations in at least one environmental sample. than 10 (table 8), indicating that iron reduction was the domi- Benzene was detected in the sample from well JH–1.5D nant redox process at that time (Chapelle and others 2009). collected during April 2012, ethylbenzene was detected in Methanogenesis was identified as a dominant process twice the sample from well JH–2.5 collected during June 2011, and during the study, once at well JH–1.5 during June 2011 and once at well JH–3 during July 2011. High dissolved methane xylene was detected in the samples from well JH–2.5 collected concentrations were measured in samples from both wells during June and July 2011. Because the quantified benzene JH–1.5 and JH–3 (appendix 6) during June 2011, indicating concentration from well JH–1.5D is less than five times the methanogenesis had taken place in the aquifer in the vicin- concentration measured in the trip blank, the value from the ity of these wells. Dissolved methane gas also was detected environmental sample has been qualified (appendix 7). None in samples from wells JH–1.5D, JH–2.5, JH–3D, and JH–3.5 of the compounds described in this paragraph were detected (appendix 6), indicating methanogenesis also has taken place during the previous baseline study, or consistently during this in the vicinity of these wells. followup study. Several possible reasons these compounds Concentrations of DOC, a potential carbon source for were not consistently detected include (1) these compounds heterotrophic bacteria, generally were low in samples from are present in the aquifer at concentrations near the analytical all 10 wells, ranging from an estimated 0.36 to 4.12 mg/L MDL and are difficult to detect, (2) these compounds were not (table 7; appendix 5). DOC was detected in at least one sample from a persistent source during this study, and (3) these com- from each well during the study (appendix 5) and in a field- pounds were detected because of contamination introduced equipment blank collected during July 2011 (appendix 3). during sampling or analysis. Water Quality 29 Table 8. Assignment of redox categories and processes for groundwater samples from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

– 2+ 2+ 2– [mg/L, milligrams per liter; NO3 , nitrate; --, not applicable; Mn , manganous manganese; µg/L, micrograms per liter; Fe , ferrous iron; SO4 , sulfate; H2S, – 2– dihydrogen sulfide; HS hydrogen sulfide; S , sulfide; General redox category: 2O ≥0.5 mg/L, dissolved oxygen greater than or equal to 0.5 mg/L; O2<0.5 mg/L, dissolved oxygen less than 0.5 mg/L; Redox process: O2, oxygen reduction; Mn(IV), manganese reduction; CH4gen, methanogenesis; Fe(III), iron reduction;

SO4, sulfate reduction; NO3 nitrate reduction]

NO – Sulfide Dissolved 3 Fe2+/ Sample Sample (as Mn2+ Fe2+ SO 2– (sum of H S, General redox Redox oxygen 4 2 sulfide date time nitrogen) (µg/L) (µg/L) (mg/L) HS–, S2–) category process (mg/L) ratio (mg/L) (mg/L) Well JH–1 1 06/08/2011 1200 9 -- 0.16 3.2 9.75 -- O2≥0.5 mg/L Unknown --

07/19/2011 1030 -- -- 0.16 3.4 -- -- O2≥0.5 mg/L Unknown --

11/01/2011 1100 8.2 -- 0.16 3.2 -- -- O2≥0.5 mg/L Unknown --

04/03/2012 1030 7.7 0.286 0.16 3.2 10.80 -- Oxic O2 -- Well JH–1.5 06/10/2011 1030 0.1 0.023 967 23.9 1.99 0.002 Anoxic Mn(IV) -- 07/20/2011 1800 0.2 0.2 3,040 843 0.24 0.0075 Anoxic CH4gen -- Well JH–1.5R

11/02/2011 1730 0.3 -- 1,640 230 -- 0 O2<0.5 mg/L Unknown -- 04/04/2012 1820 0.1 0.04 1,120 153 9.43 0.002 Anoxic Fe(III) 76.50 Well JH–1.5D 06/10/2011 1150 0.2 0.02 907 470 5.64 0.005 Anoxic Fe(III) 94.00 07/20/2011 1930 0.1 0.02 1,130 1,050 1.01 0.0545 Anoxic Fe(III) 19.27

11/03/2011 1300 0.1 -- 1,450 931 7.95 0.003 O2<0.5 mg/L Unknown -- 04/05/2012 1020 0.1 0.04 1,160 617 9.58 0.007 Anoxic Fe(III) 88.14 Well JH–2

06/08/2011 1710 4.3 1.34 0.16 3.2 8.05 0 Oxic O2 --

07/19/2011 1530 4.7 0.764 0.16 3.2 11.20 0.08 Oxic O2 --

11/01/2011 1510 3.3 -- 0.16 3.2 -- -- O2≥0.5 mg/L Unknown --

04/03/2012 1530 4.1 0.197 0.32 3.2 11.60 -- Oxic O2 -- Well JH–2.5 06/09/2011 1500 0.2 0.037 108 3.2 6.59 0.005 Anoxic Mn(IV) -- 07/21/2011 1100 0.3 0.018 61.7 7.2 4.53 0.005 Anoxic Mn(IV) --

11/03/2011 1430 0.1 -- 135 5.7 -- 0.005 O2<0.5 mg/L Unknown --

04/04/2012 0950 1.0 0.04 8.92 47.1 11.00 0.005 Oxic O2 -- Well JH–3 06/09/2011 1830 0.1 0.02 1,690 584 3.52 0.006 Anoxic Fe(III) 97.33

07/20/2011 1100 0.2 0.013 1,730 735 0.16 0.024 Anoxic CH4gen --

11/02/2011 1350 0.1 -- 1,530 515 -- 0.005 O2<0.5 mg/L Unknown -- 04/04/2012 1250 0.1 0.04 1,090 254 9.5 0.009 Anoxic Fe(III) 28.22 Well JH–3D 06/09/2011 2030 0.1 0.02 1,030 592 5.43 0.008 Anoxic Fe(III) 74.00 07/20/2011 1300 0.1 0.02 1,060 572 1.87 0.02 Anoxic Fe(III) 28.60

11/02/2011 1510 0.2 -- 898 648 -- 0.012 O2<0.5 mg/L Unknown -- 04/04/2012 1450 0.1 0.04 769 493 8.92 0.023 Anoxic Fe(III) 21.43 Well JH–3.5 06/09/2011 1000 0.3 0.03 21.3 7.1 8.14 0.005 Suboxic Suboxic --

07/21/2011 1430 0.2 -- 806 8.1 0.43 0.005 O2<0.5 mg/L Unknown --

11/02/2011 1110 0.1 -- 1,610 760 -- 0.011 O2<0.5 mg/L Unknown -- Well JH–4

06/08/2011 1500 8.2 -- 0.21 3.2 7.71 -- O2≥0.5 mg/L Unknown --

07/19/2011 1300 8.0 -- 0.26 10.9 -- -- O2≥0.5 mg/L Unknown --

11/01/2011 1330 8.0 -- 0.16 3.7 -- -- O2≥0.5 mg/L Unknown --

04/03/2012 1300 7.5 0.168 0.18 4.2 8.48 -- Oxic O2 -- 1Dissolved-oxygen concentration measured by laboratory was an average of 7.1 mg/L. This field measurement is questionable and only presented in this table to show sample was oxic. This value was not used in analysis. 30 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Small concentrations of DROs in the C10–C36 and concentrations of 4-MeBT ranged from an estimated 0.37 to

C10–C32 ranges were detected in several samples collected 9.8 µg/L with most detections an order of magnitude greater during the baseline study (Wright, 2010) from wells JH–1, than the LRL. The measurable concentrations of 5-MeBT were JH–2, and JH–4. The source of the low-level DRO concentra- all estimated and ranged from 0.26 to 0.77 µg/L. The triazole tions in samples from the wells, including well JH–1, which is 4-MeBT was detected consistently in greater concentrations upgradient from all airport operations, is not known. During than 5-MeBT (appendix 8). This pattern in the data is consis- the followup study, samples collected from all monitor wells tent with other triazole research, which determined 5-MeBT during June and July 2011 and April 2012 were analyzed for is more biodegradable, whereas 4-MeBT is more recalcitrant DROs. The DROs were not detected during this followup (Cornell, 2002; Weiss and Reemtsma, 2005). The highest study (appendix 7). concentrations of 4-MeBT and 5-MeBT were in samples from Triazoles were detected in 7 of the 10 wells sam- wells JH–1.5D and JH–1.5R, respectively, during Novem- pled (appendix 8). Only two of the three triazoles mea- ber 2011. Triazoles were detected only in monitor wells with sured, 4-MeBT and 5-MeBT, were detected. Measurable reducing conditions.

A B 10 10 9 8 8 7 6 6 5 4 4 3 2 2 1 0 0 200 300 400 500 600 700 1 10 100 1,000 10,000 Specific conductance, in microsiemens per centimeter at 25 degrees Celsius Dissolved iron concentration, in micrograms per liter C D 10 10

8 8

6 6

4 4 Dissolved-oxygen concentration, in micrograms per liter

2 2

0 0 0.1 1 10 100 1,000 10,000 0 5 10 15 Dissolved manganese concentration, in micrograms per liter 4-Methyl-1H-benzotriazole concentration, in micrograms per liter

EXPLANATION

Upgradient and lateral wells

Downgradient wells

Figure 8. Bivariate graphs showing the relations between concentrations of dissolved oxygen and as compared to selected properties value or constituents measured in groundwater-quality samples collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012. A, specific conductance; B, dissolved iron; C, dissolved manganese; and manganese; D, 4-methyl-1H- benzotriazole. Summary 31

Implications for Reduced Groundwater organic carbon or oxidizable minerals (Appelo and Postma, 2005; Drever, 1997; Hem, 1989). The source of organic Conditions carbon causing reduced groundwater conditions downgradient from airport operations could not be directly determined; how- During the baseline study at the JHA, Wright (2010) ever, the detection of triazoles in groundwater directly down- reported that a zone of highly reduced groundwater had been gradient from airport operations (fig. 7) is important because observed downgradient from airport operations. The chemical these compounds are not naturally occurring and often are conditions in the groundwater were indicative of the presence additives in human made products used at the airport, includ- of organic compounds such as those present in fuels, ADAFs, ing ADAFs. The detection of triazoles associated with ADAFs or their breakdown products; however, none of the organic in samples from wells downgradient from airport operations compounds were detected at substantial concentrations in the makes a natural cause for the reduced conditions unlikely. It groundwater, and the source of reducing conditions was not is more likely that ADAFs or pavement deicers have seeped determined. The addition of several new monitor wells and into the groundwater system. Although triazole concentrations water-quality analyses for this followup study have provided detected at the airport are not of toxicological significance a better understanding of the groundwater conditions at (Cancilla and others 1998, 2003b; Corsi and others, 2006a), the JHA. it should be noted that Cancilla and others (1997) identified Groundwater from all of the new monitor wells (JH–1.5, triazoles as the additives in formulated ADAF mixtures that JH–1.5R, JH–1.5D, JH–2.5, and JH–3.5) installed for the are toxic to microorganisms. followup study had water-quality characteristics similar to characteristics in groundwater from wells JH–3 and JH–3D. A series of graphs (fig. 8) show the relations between concentrations of dissolved oxygen as compared to A, specific Summary conductance; B dissolved iron; C dissolved manganese; and D, 4-MeBT. Wells that are upgradient from and lateral to Groundwater levels were measured in and groundwater- airport deicing operations (blue symbols) are wells JH–1, quality samples were collected from wells completed in the JH–2, and JH–4; wells that are downgradient from airport Snake River alluvial aquifer at the Jackson Hole Airport in deicing operations (red symbols) are wells JH–1.5, JH–1.5R, northwestern Wyoming during water years 2011 and 2012 JH–1.5D, JH–2.5, JH–3, JH–3D, and JH–3.5. The graphs in for a followup study to a previous baseline study conducted figure 8A, B, and C show that samples of groundwater with during 2008––09. This followup study was conducted by the low concentrations of dissolved oxygen (reduced condi- U.S. Geological Survey, in cooperation with the Jackson Hole tions) had higher values of specific conductance and higher Airport Board, to further characterize the hydrogeology and concentrations of dissolved iron and dissolved manganese, groundwater quality of the Snake River aquifer in upgradient respectively. Additionally, these graphs show that the values of and downgradient parts of the aquifer underlying the airport. specific conductance and concentrations of dissolved iron and Five new wells were installed upgradient from and later- dissolved manganese detected in upgradient and lateral wells ally to selected monitoring wells installed for the baseline are distinctly different from the values and concentrations of study. Groundwater-level measurements were collected from these constituents detected in the wells downgradient from 19 wells and groundwater-quality analyses from a subset of airport operations. The compound 4-MeBT was only detected 10 of these wells. Data, including groundwater levels, field in measurable concentrations in downgradient monitor wells measurements of physical properties of water, major ions, (fig. 8D) with low dissolved-oxygen concentrations. Although nutrients, volatile organic compounds (VOCs), gasoline-range well JH–2 has been included in analyses as a well lateral to organics (GROs), diesel-range organics (DROs), triazoles, the reduced groundwater zone, it should be noted the aver- dissolved gases, and miscellaneous field and laboratory age dissolved-oxygen concentration measured at well JH–2 analytical results, are presented in this report. The direc- dropped from 6.7 mg/L during the period 2008–09 (Wright, tion of groundwater flow, hydraulic gradients, and estimated 2010) to 4.1 mg/L during the period 2011–12. groundwater velocity rates of the Snake River alluvial aquifer When compared to USEPA water-quality standards and underlying the study area also are presented, and the reduction health advisories (U.S. Environmental Protection Agency, and oxidation (redox) condition is characterized for selected 2012), the water quality in the Snake River alluvial aquifer at well locations. the airport generally is high quality and considered to be suit- Water levels collected throughout the followup study able for domestic and other uses without treatment. However, indicate the water table was lowest in the early spring and water-quality results for some constituents (figs. 7 and 8) in reached its peak in July or August, with an increase of 12.5 to samples from wells downgradient from the airport terminal 15.5 feet between April and July of 2011. Water-table contour (fig. 5A) commonly were different than water-quality results maps show that the water table was highest in the northeast for wells upgradient from and lateral to the groundwater flow part of the airport and lowest in the southwest, indicating path. Reducing conditions present in an otherwise oxic aquifer that the direction of groundwater flow generally was to the system indicate an upgradient or a natural, in place, source of west-southwest. The water table dropped about 22 feet across 32 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming the airport with an average hydraulic gradient of 0.0068 foot/ oxygen in groundwater in the Snake River alluvial aquifer foot, which slightly is higher than the average of 0.0066 foot was identified using a spreadsheet model designed to use a per foot determined during the baseline study. Generally, the multiple-line-of-evidence approach to distinguish the source vertical hydraulic gradient was small, averaging 0.005 foot per of reduction. Results indicate iron reduction is the dominant foot. Lithologic data for monitoring wells JH–1 through JH–4, redox process; however, the model indicated manganese coupled with a fairly narrow range of hydraulic gradients for reduction and methanogenesis also are active redox processes these wells, indicate the Snake River alluvial aquifer at the at the JHA. airport is relatively homogeneous. The horizontal ground- Samples from all of the wells included in the followup water velocity in the alluvial aquifer was estimated to be 25 study were analyzed for anthropogenic compounds; only to 68 feet per day. The travel time from the farthest upgradi- samples collected from the five new wells were analyzed for ent well to the farthest downgradient well was approximately VOCs and GROs, whereas samples from all of the wells were 52 to 142 days. This estimate of groundwater velocity only analyzed for DROs and triazoles. GROs, benzene, ethylben- describes the movement of water through the aquifer because zene, and total xylene each were detected (but reported as solutes may move at a different rate. estimated concentrations) in at least one groundwater sample. Generally, water in the Snake River alluvial aquifer These compounds were not detected during the previous study was determined to be of good quality. No constituents were or consistently during this study. Several possible reasons detected at concentrations exceeding U.S. Environmental these compounds were not detected consistently include Protection Agency (USEPA) Maximum Contaminant Levels (1) these compounds are present in the aquifer at concentra- or health advisories; however, redox measurements indicate tions near the analytical method detection limit and are dif- oxygen-poor water in many of the wells. Gasoline-range ficult to detect, (2) these compounds were not from a persis- organics, three volatile organic compounds, and triazoles were tent source during this study, and (3) these compounds were detected in some groundwater samples. Although the quality detected because of contamination introduced during sampling of groundwater in the shallow aquifer generally was suitable or analysis. for domestic and other uses without treatment, two inorganic DROs were detected during the baseline study but were constituents (dissolved iron and dissolved manganese) were not detected in any samples during the followup study. Two of detected at concentrations exceeding USEPA Secondary Maxi- the three triazoles (4-methyl-1H-benzotriazole and 5-methyl- mum Contaminant Levels in some samples. 1H-benzotriazole) were detected at low concentrations in 7 of Specific-conductance values ranged from 247 to the 10 wells sampled. 622 microsiemens per centimeter at 25 degrees Celsius, and In general, low dissolved-oxygen concentrations and pH values were neutral to alkaline. Dissolved solids and reducing conditions present at many airport monitoring wells major-ion data indicated the groundwater sampled at the air- are not uncommon in groundwater; however, dissolved- port is considered hard to very hard, fresh, calcium bicarbon- oxygen concentrations in water from other wells sampled ate water. Dissolved-oxygen concentrations ranged from less at the Jackson Hole Airport were 3.3 milligrams per liter or than 0.1 to 9.0 milligrams per liter indicating some variability higher, indicating the Snake River alluvial aquifer naturally is in the oxygen content of the aquifer underlying the airport. oxic in the vicinity of the airport. Reducing conditions in an Although oxic aquifer conditions were indicated for three of otherwise oxic aquifer system are indicative of an upgradient the wells, dissolved-oxygen concentrations indicated reducing or in place source of organic carbon. The detection of triazoles conditions at the seven remaining wells. in groundwater downgradient from airport operations makes it Nutrients were detected at low concentrations in all unlikely there is a natural cause for the high rates of reduction samples collected. Nitrate is the primary dissolved-nitrogen present in many airport monitor wells. It is more likely that species in the aquifer. In samples in which nitrate was not aircraft deicers, anti-icers, or pavement deicers have seeped detected, ammonia was detected. Dissolved organic carbon into the groundwater system. was detected in all of the wells at concentrations within the estimated range for natural groundwater (0 to 3 milligrams per liter) except one sample, which was greater than the estimated range for natural groundwater and had a concentration a References Cited magnitude higher than other dissolved organic carbon concentrations measured in this followup study. Chemical oxygen Appelo, C.A.J., and Postma, Dieke, 2005, Geochemistry, demand was not detected in any samples. groundwater and pollution (2d ed.): Leiden, The Nether- Dissolved gas samples were collected and hydrogen lands, A.A. Balkema Publishers, 649 p. sulfide, low-level dissolved oxygen, and ferrous iron were analyzed in the field to better understand the redox conditions Breedveld, G.D., Roseth, R., Sparrevik, M., Hartnik, T., and of the alluvial aquifer. These additional analyses confirmed the Hem, L.J., 2003, Persistence of the de-icing additive ben- low concentrations of dissolved oxygen and indicated the pres- zotriazole at an abandoned airport: Water, Air, and Pollu- ence of low concentrations of methane gas in samples from tion—Focus, v. 3, no. 3, p. 91–101. (Also available at http:// several wells. The biological redox status of low dissolved dx.doi.org/10.1023/A:1023961213839.) References Cited 33

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Appendix 1. Well construction and related ancillary information for wells used for data collection at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

[USGS, U.S. Geological Survey; SS, south side; NAD 83, North American Datum of 1983; °, degrees; ʹ, minutes; ʺ, seconds; ft, feet; bls, below land surface; MP, measuring point; --, not able to measure or find listed; -XX, a negative MP indicates a measurement above land surface; NAVD 88, North American Vertical Datum of 1988; PVC, polyvinyl chloride; na, value is not available]

Depth Depth to Elevation Well Height USGS site identifi- Well Latitude Longitude to top of bottom of of MP, Description depth, of MP cation number identifier (NAD 83) (NAD 83) screen screen ft above of MP ft, bls ft ft, bls ft, bls NAVD 88 Water-quality and water levels 433615110440001 JH–1 43°36ʹ14.55ʺ 110°44ʹ02.31ʺ 60.36 30 50 0.55 6,421.91 Top of PVC casing. 433604110443401 JH–1.5 43°36ʹ04.2ʺ 110°44ʹ03.5ʺ 55 45 55 -1.26 6,415.52 Top of PVC casing. 433604110443403 JH–1.5R 43°36ʹ04.25ʺ 110°44ʹ33.58ʺ 64 44 64 -0.48 6,415.88 Top of PVC casing. 433604110443402 JH–1.5D 43°36ʹ04.2ʺ 110°44ʹ33.5ʺ 94.45 85 95 -0.40 6,416.05 Top of PVC casing. 433551110443501 JH–2 43°35ʹ50.69ʺ 110°44ʹ37.54ʺ 59.45 30 55 0.32 6,406.27 Top of PVC casing. 433600110443701 JH–2.5 43°35ʹ59.8ʺ 110°44ʹ37.5ʺ 55.0 45 55 0.25 6,412.72 Top of PVC casing. 433603110443501 JH–3 43°36ʹ02.92ʺ 110°44ʹ37.31ʺ 60.23 40 60 0.28 6,411.94 Top of PVC casing. 433603110443502 JH–3D 43°06ʹ02.65ʺ 110°44ʹ37.45ʺ 102.58 -- -- -1.97 6,413.96 Top of steel casing. 433605110443801 JH–3.5 43°36ʹ04.97ʺ 110°44ʹ37.57ʺ 55.0 45 55 0.31 6,410.51 Top of PVC casing. 433613110443501 JH–4 43°36ʹ12.48ʺ 110°44ʹ37.70ʺ 58.87 40 55 0.32 6,417.74 Top of PVC casing. Water levels only 433556110441601 Hangar 5 43°35ʹ55.94ʺ 110°44ʹ18.76ʺ 92 na na 0.25 6,409.61 Top of steel casing. 433630110442701 Control tower 43°06ʹ29.45ʺ 110°44ʹ30.02ʺ 100 na na -1.07 6,428.62 Top of well cap. 433604110441001 SS gas tanks 43°36ʹ03.36ʺ 110°44ʹ12.81ʺ 55.70 na na 0.12 6,416.51 Top of well cap. 433606110440501 Airport 43°36ʹ05.64ʺ 110°44ʹ07.94ʺ 81 na na -1.17 6,418.34 Top of well entrance cap. 433605110441201 Hangar 2 43°36ʹ04.93ʺ 110°44ʹ14.51ʺ 89 na na -1.26 6,418.09 Top of well cap. 433602110441201 Hangar 3 43°36ʹ02.01ʺ 110°44ʹ14.50ʺ -- na na -1.02 6,415.11 Top of well cap. 433558110441501 Auto garage 43°05ʹ57.57ʺ 110°44ʹ17.43ʺ -- na na 0.26 6,412.31 Top of steel casing. 433607110440901 Hangar 1 43°36ʹ06.4ʺ 110°44ʹ11.94ʺ 65 na na -1.24 6,419.75 Top of steel casing. Appendixes 39

Appendix 2. Water-level data and related ancillary information for measurements collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

[SS, south side; BLS, below land surface; e-tape, calibrated electric tape; NAVD 88, North American Vertical Datum of 1988; --, not applicable]

Well identifier Time Water level Water level Water-level altitude, Date (fig. 2) (24 hour) (feet BLS) method (feet above NAVD 88) JH–1 11/2/2010 0900 41.76 e-tape 6,380.70 3/22/2011 1130 47.1 e-tape 6,375.36 5/9/2011 1800 42.67 e-tape 6,379.79 6/8/2011 0940 38.17 e-tape 6,384.29 7/19/2011 0847 33.34 e-tape 6,389.12 8/10/2011 1600 33.28 e-tape 6,389.18 11/1/2011 0920 39.1 e-tape 6,383.36 4/3/2012 0855 44.89 e-tape 6,377.57 7/17/2012 0930 37.09 e-tape 6,385.37 8/21/2012 1500 39.22 e-tape 6,383.24 JH–1.5 11/3/2010 0934 51.42 e-tape 6,362.84 2/10/2011 1255 Dry e-tape -- 3/15/2011 1430 Dry e-tape -- 5/9/2011 1540 50.8 e-tape 6,363.46 6/10/2011 0818 46.46 e-tape 6,367.80 7/20/2011 1600 43.36 e-tape 6,370.90 8/10/2011 1310 43.33 e-tape 6,370.93 10/19/2011 1625 47.02 e-tape 6,370.24 7/17/2012 1122 45.24 e-tape 6,369.02 JH–1.5R 11/2/2011 1625 49.28 e-tape 6,366.12 4/4/2012 1720 54.76 e-tape 6,360.64 7/17/2012 1120 46.38 e-tape 6,369.02 8/21/2012 1611 48.84 e-tape 6,366.56 JH–1.5D 11/3/2010 1520 52.01 e-tape 6,363.24 2/10/2011 1300 56.46 e-tape 6,358.79 3/15/2011 1500 57.22 e-tape 6,358.03 5/9/2011 1615 51.36 e-tape 6,363.89 6/10/2011 0820 47.06 e-tape 6,368.19 7/20/2011 1602 43.94 e-tape 6,371.31 8/10/2011 1158 45.16 steel tape 6,370.09 11/3/2011 0915 49.55 e-tape 6,365.70 4/5/2012 0835 54.94 e-tape 6,360.31 7/17/2012 1125 46.23 e-tape 6,369.02 8/21/2012 1608 49 e-tape 6,366.25 JH–2 11/2/2010 1600 48.53 e-tape 6,358.06 2/10/2011 1330 53.51 e-tape 6,353.08 3/15/2011 1700 54.35 e-tape 6,352.24 5/9/2011 1720 48.34 e-tape 6,358.25 6/8/2011 1610 42.83 e-tape 6,363.76 7/19/2011 1417 39.21 e-tape 6,367.38 10/19/2011 1808 44.73 e-tape 6,361.86 11/1/2011 1442 45.85 e-tape 6,360.74 4/3/2012 1415 52.16 e-tape 6,354.43 7/17/2012 1013 42.46 e-tape 6,364.13 8/21/2012 1621 45.5 e-tape 6,361.09 40 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Appendix 2. Water-level data and related ancillary information for measurements collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.—Continued

[SS, south side; BLS, below land surface; e-tape, calibrated electric tape; NAVD 88, North American Vertical Datum of 1988; --, not applicable]

Well identifier Time Water level Water level Water-level altitude, Date (fig. 2) (24 hour) (feet BLS) method (feet above NAVD 88) JH–2.5 2/10/2011 1310 54.55 e-tape 6,358.42 3/15/2011 1630 Dry e-tape -- 5/9/2011 1705 49.49 e-tape 6,363.48 6/9/2011 1358 44.82 e-tape 6,368.15 7/21/2011 0917 41.68 e-tape 6,731.29 10/19/2011 0910 46.55 e-tape 6,366.42 11/3/2011 1334 47.87 e-tape 6,365.10 4/4/2012 0830 53.51 e-tape 6,359.46 7/17/2012 1105 44.69 e-tape 6,368.28 8/21/2012 1616 47.36 e-tape 6,365.61 JH–3 2/10/2011 1240 55.5 e-tape 6,356.72 3/15/2012 1330 56.27 e-tape 6,355.95 5/9/2011 1435 50.3 e-tape 6,361.92 6/9/2011 1652 45.97 e-tape 6,366.25 7/20/2011 0825 43.11 e-tape 6,369.11 10/19/2011 0858 47.72 e-tape 6,364.50 11/2/2011 1238 48.97 e-tape 6,363.25 4/4/2012 1132 54.51 e-tape 6,357.71 7/17/2012 1131 45.94 e-tape 6,366.28 8/21/2012 1559 48.51 e-tape 6,363.71 JH–3D 2/10/2011 1250 55.6 e-tape 6,356.39 3/15/2011 1340 56.4 e-tape 6,355.59 5/9/2011 1500 50.31 e-tape 6,361.68 6/9/2011 1658 45.93 e-tape 6,366.06 7/20/2011 0828 43.04 e-tape 6,368.95 10/19/2011 0902 47.72 e-tape 6,364.27 11/2/2011 1220 48.96 e-tape 6,363.03 4/4/2012 1135 54.66 e-tape 6,357.33 7/17/2012 1136 45.95 e-tape 6,366.04 8/21/2012 1603 48.52 e-tape 6,363.47 JH–3.5 11/3/2010 0820 50.31 e-tape 6,360.51 2/10/2011 1230 54.59 e-tape 6,356.23 3/15/2011 1245 54.6 e-tape 6,356.22 5/9/2011 1415 50.55 e-tape 6,360.27 6/9/2011 0830 46.4 e-tape 6,364.42 7/21/2011 1242 43.58 e-tape 6,367.24 10/19/2011 0918 48.13 e-tape 6,362.69 11/2/2011 0938 49.39 e-tape 6,361.43 4/3/2012 1615 54.61 e-tape 6,356.21 7/17/2012 1140 45.39 e-tape 6,365.43 8/21/2012 1554 48.89 e-tape 6,361.93 Appendixes 41

Appendix 2. Water-level data and related ancillary information for measurements collected from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.—Continued

[SS, south side; BLS, below land surface; e-tape, calibrated electric tape; NAVD 88, North American Vertical Datum of 1988; --, not applicable]

Well identifier Time Water level Water level Water-level altitude, Date (fig. 2) (24 hour) (feet BLS) method (feet above NAVD 88) JH–4 11/2/2010 1320 54.04 e-tape 6,364.02 2/10/2011 1220 58.19 e-tape 6,359.87 3/15/2011 1145 58.91 e-tape 6,359.15 5/9/2011 1330 52.82 e-tape 6,365.24 6/8/2011 1403 49.35 e-tape 6,368.71 7/19/2011 1155 46.93 e-tape 6,371.13 10/19/2011 1155 50.98 e-tape 6,367.08 11/1/2011 1240 52.11 e-tape 6,365.95 4/3/2012 1144 57.44 e-tape 6,360.62 7/17/2012 1145 49.45 e-tape 6,368.61 8/21/2012 1539 51.69 e-tape 6,366.37 Hangar 1 11/1/2011 1210 40.2 steel tape 6,376.35 4/3/2012 1830 46.03 steel tape 6,370.48 8/21/2012 1452 41.1 steel tape 6,375.41 Hangar 5 11/1/2011 1630 36.59 e-tape 6,373.27 4/3/2012 1725 42.52 e-tape 6,367.34 7/18/2012 1445 34.13 e-tape 6,375.73 8/21/2012 1635 36.59 e-tape 6,373.27 Control Tower 7/19/2011 1720 48.9 steel tape 6,378.66 11/1/2011 1604 53.38 steel tape 6,374.17 4/3/2012 1655 58.17 steel tape 6,369.38 7/17/2012 1155 51.24 e-tape 6,376.31 8/21/2012 1501 52.95 steel tape 6,374.60 SS fuel farm 11/1/2011 1710 39.12 e-tape 6,377.51 4/3/2012 1756 44.97 e-tape 6,371.66 7/18/2012 1520 36.92 e-tape 6,379.71 8/21/2012 1655 38.37 e-tape 6,378.26 Airport Entrance 11/1/2011 1200 37.63 steel tape 6,379.54 4/3/2012 1835 43.62 steel tape 6,373.55 7/18/2012 0730 35.46 e-tape 6,381.71 8/21/2012 1445 37.76 steel tape 6,379.41 Hangar 2 11/1/2011 1720 39 steel tape 6,377.83 4/3/2012 1812 44.79 steel tape 6,372.04 7/18/2012 1530 36.77 e-tape 6,380.06 8/21/2012 1701 40.04 steel tape 6,376.79 Hangar 3 11/1/2011 1652 37.73 steel tape 6,376.36 4/3/2012 1747 43.55 steel tape 6,370.54 7/18/2012 1511 35.47 e-tape 6,378.62 8/21/2012 1646 37.74 steel tape 6,376.35 Auto Garage 11/1/2011 1645 38.66 e-tape 6,373.91 4/3/2012 1738 44.5 e-tape 6,368.07 7/18/2012 1505 36.16 e-tape 6,376.41 8/21/2012 1641 38.69 e-tape 6,373.88 42 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Appendix 3. Inorganic and organic constituents in blank samples collected for followup study at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

[mg/L, milligrams per liter; --, not applicable; <, less than symbol indicates the chemical was not detected and the value following the less than symbol is the laboratory reporting level; Bold value indicates constituent was detected above reporting level; µg/L, micrograms per liter; E, estimated concentration]

Trip blanks Field equipment blanks Physical property or constituent Units JH–1.5 JH–1 JH–1.5R JH–2.5 JH–2.5 JH–3 JH–1.5R 06/10/2011 07/19/2011 04/04/2012 06/09/2011 07/21/2011 07/20/2011 04/04/2012 Major ions and related characteristics (in filtered water unless noted) Chemical oxygen demand, high mg/L ------<10 -- <10 <10 level, total Dissolved solids mg/L ------<12 -- <12 <20 Hardness, total, as calcium mg/L ------<0.09 -- <0.09 <0.10 carbonate Calcium mg/L ------<0.022 -- <0.022 <0.022 Magnesium mg/L ------<0.008 -- <0.008 <0.011 Potassium mg/L ------<0.02 -- <0.02 <0.03 Sodium mg/L ------<0.06 -- <0.06 <0.06 Bromide mg/L ------<0.010 -- <0.010 <0.010 Chloride mg/L ------<0.06 -- <0.06 <0.06 Fluoride mg/L ------<0.04 -- <0.04 <0.04 Silica as silicon dioxide mg/L ------<0.029 -- <0.029 <0.018 Sulfate mg/L ------<0.09 -- <0.09 <0.09 Nutrients (filtered water unless noted) Ammonia as nitrogen mg/L ------<0.010 -- <0.010 0.014 Nitrate plus nitrite as nitrogen mg/L ------<0.02 -- <0.02 <0.040 Nitrite as nitrogen mg/L ------<0.001 -- <0.001 <0.001 Orthophosphate as phosphorus mg/L ------<0.004 -- <0.004 <0.004 Phosphorus as phosphorus, total mg/L ------0.006 -- 0.005 <0.004 Total nitrogen (nitrate plus mg/L ------<0.05 -- <0.05 <0.05 nitrite plus ammonia plus organic-nitrogen) Organic carbon mg/L ------<0.15 0.22 -- <0.23 Trace elements (in filtered water) Iron µg/L ------<3.2 -- <3.2 <3.2 Manganese µg/L ------<0.16 -- 0.6 0.19 Volatile organic compounds (VOCs) 1,2,3-Trichloropropane µg/L <0.2 <0.2 <0.2 <0.2 <0.2 -- <0.2 1,2-Dibromo-3-chloropropane µg/L <0.300 <0.300 <0.300 <0.300 <0.300 -- <0.300 1,2-Dibromoethane µg/L <0.2000 <0.2000 <0.2000 <0.2000 <0.2000 -- <0.2000 1,2-Dichloroethane µg/L <0.17 <0.17 <0.17 <0.17 <0.17 -- <0.17 1,2-Dichloropropane µg/L <0.45 <0.45 <0.45 <0.45 <0.45 -- <0.45 1,3-Dichloropropane µg/L <0.430 <0.430 <0.430 <0.430 <0.430 -- <0.430 1,4-Dichlorobenzene µg/L <0.180 <0.180 <0.180 <0.180 <0.180 -- <0.180 Bromomethane µg/L <0.450 <0.450 <0.450 <0.450 <0.450 -- <0.450 cis-1,3-Dichloropropene µg/L <0.32 <0.32 <0.32 <0.32 <0.32 -- <0.32 trans-1,3-Dichloropropene µg/L <0.5 <0.5 <0.5 <0.5 <0.5 -- <0.5 1,1,1,2-Tetrachloroethane µg/L <0.2 <0.2 <0.2 <0.2 <0.2 -- <0.2 Appendixes 43

Appendix 3. Inorganic and organic constituents in blank samples collected for followup study at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.—Continued

Trip blanks Field equipment blanks Physical property or constituent Units JH–1.5 JH–1 JH–1.5R JH–2.5 JH–2.5 JH–3 JH–1.5R 06/10/2011 07/19/2011 04/04/2012 06/09/2011 07/21/2011 07/20/2011 04/04/2012 1,1,1-Trichloroethane µg/L <0.27 <0.27 <0.27 <0.27 <0.27 -- <0.27 1,1,2,2-Tetrachloroethane µg/L <0.18 <0.18 <0.18 <0.18 <0.18 -- <0.18 1,1,2-Trichloroethane µg/L <0.22 <0.22 <0.22 <0.22 <0.22 -- <0.22 1,1-Dichloroethane µg/L <0.390 <0.390 <0.390 <0.390 <0.390 -- <0.390 1,1-Dichloroethene µg/L <0.32 <0.32 <0.32 <0.32 <0.32 -- <0.32 1,1-Dichloropropene µg/L <0.19 <0.19 <0.19 <0.19 <0.19 -- <0.19 1,2,3-Trichlorobenzene µg/L <0.14 <0.14 <0.14 <0.14 <0.14 -- <0.14 1,2,4-Trichlorobenzene µg/L <0.18 <0.18 <0.18 <0.18 <0.18 -- <0.18 1,2,4-Trimethylbenzene µg/L <0.170 <0.170 <0.170 <0.170 <0.170 -- <0.170 1,2-Dichlorobenzene µg/L <0.170 <0.170 <0.170 <0.170 <0.170 -- <0.170 1,3,5-Trimethylbenzene µg/L <0.160 <0.160 <0.160 <0.160 <0.160 -- <0.160 1,3-Dichlorobenzene µg/L <0.140 <0.140 <0.140 <0.140 <0.140 -- <0.140 2,2-Dichloropropane µg/L <0.310 <0.310 <0.310 <0.310 <0.310 -- <0.310 2-Chlorotoluene µg/L <0.170 <0.170 <0.170 <0.170 <0.170 -- <0.170 4-Chlorotoluene µg/L <0.160 <0.160 <0.160 <0.160 <0.160 -- <0.160 4-Isopropyltoluene µg/L <0.210 <0.210 <0.210 <0.210 <0.210 -- <0.210 Benzene µg/L <0.18 <0.065 E .080 <0.065 <0.065 -- <0.18 Benzotriazole µg/L ------<0.250 <0.250 -- <0.250 Bromobenzene µg/L <0.4 <0.4 <0.4 <0.4 <0.4 -- <0.4 Bromochloromethane µg/L <0.300 <0.300 <0.300 <0.300 <0.300 -- <0.300 Bromodichloromethane µg/L <0.54 <0.54 <0.54 <0.54 <0.54 -- <0.54 Chlorobenzene µg/L <0.27 <0.27 <0.27 <0.27 <0.27 -- <0.27 Chloroethane µg/L <0.33 <0.33 <0.33 <0.33 <0.33 -- <0.33 Chloromethane µg/L <0.32 <0.32 <0.32 <0.32 <0.32 -- <0.32 cis-1,2-Dichloroethene µg/L <0.37 <0.37 <0.37 <0.37 <0.37 -- <0.37 Dibromochloromethane µg/L <0.430 <0.430 <0.430 <0.430 <0.430 -- <0.430 Dibromomethane µg/L <0.38 <0.38 <0.38 <0.38 <0.38 -- <0.38 Dichlorodifluoromethane µg/L <0.34 <0.34 <0.34 <0.34 <0.34 -- <0.34 Methylene chloride µg/L 0.66 1.3 <0.36 <0.36 <0.36 -- <0.36 Ethylbenzene µg/L <0.12 <0.10 <0.10 <0.10 <0.10 -- <0.12 Hexachlorobutadiene µg/L <0.260 <0.260 <0.260 <0.260 <0.260 -- <0.260 Isopropylbenzene µg/L <0.15 <0.15 <0.15 <0.15 <0.15 -- <0.15 Methyl tert-butyl ether µg/L <0.260 <0.260 <0.260 <0.260 <0.260 -- <0.260 m-Xylene plus p-xylene µg/L <0.420 <0.420 <0.420 <0.420 <0.420 -- <0.420 Naphthalene µg/L <0.43 <0.43 <0.43 <0.43 <0.43 -- <0.43 n-Butylbenzene µg/L <0.170 <0.170 <0.170 <0.170 <0.170 -- <0.170 n-Propylbenzene µg/L <0.170 <0.170 <0.170 <0.170 <0.170 -- <0.170 o-Xylene µg/L <0.270 <0.270 <0.270 <0.270 <0.270 -- <0.270 sec-Butylbenzene µg/L <0.140 <0.140 <0.140 <0.140 <0.140 -- <0.140 44 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Appendix 3. Inorganic and organic constituents in blank samples collected for followup study at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.—Continued

Trip blanks Field equipment blanks Physical property or constituent Units JH–1.5 JH–1 JH–1.5R JH–2.5 JH–2.5 JH–3 JH–1.5R 06/10/2011 07/19/2011 04/04/2012 06/09/2011 07/21/2011 07/20/2011 04/04/2012 Styrene µg/L <0.280 <0.280 <0.280 <0.280 <0.280 -- <0.280 tert-Butyl ethyl ether µg/L <0.26 <0.26 <0.26 <0.26 <0.26 -- -- tert-Butylbenzene µg/L <0.140 <0.140 <0.140 <0.140 <0.140 -- <0.140 Tetrachloroethene µg/L <0.30 <0.30 <0.30 <0.30 <0.30 -- <0.30 Tetrachloromethane µg/L <0.22 <0.22 <0.22 <0.22 <0.22 -- <0.22 Toluene µg/L <0.23 <0.17 <0.17 <0.17 <0.17 -- <0.23 trans-1,2-Dichloroethene µg/L <0.24 <0.24 <0.24 <0.24 <0.24 -- <0.24 Tribromomethane µg/L <0.390 <0.390 <0.390 <0.390 <0.390 -- <0.390 Trichloroethene µg/L <0.37 <0.37 <0.37 <0.37 <0.37 -- <0.37 Trichlorofluoromethane µg/L <0.230 <0.230 <0.230 <0.230 <0.230 -- <0.230 Trichloromethane µg/L <0.29 <0.29 <0.29 <0.29 <0.29 -- <0.29 Trihalomethanes µg/L <1.6 <1.6 <1.6 <1.6 <1.6 -- <1.6 Vinyl chloride µg/L <0.33 <0.33 <0.33 <0.33 <0.33 -- -- Xylene (all isomers) µg/L <0.27 <0.19 <0.19 <0.19 <0.19 -- -- Diesel range organics (DRO), gasoline range organics (GRO), and triazoles compounds Diesel range organic mg/L ------<0.057 <0.059 -- <0.510

compounds (C10-C36) Gasoline range organic µg/L -- <10 <10 <10 <10 -- <25 compounds 4-Methyl-1H-benzotriazole µg/L ------<0.35 <0.35 -- <0.35 5-Methyl-1H-benzotriazole µg/L ------<0.25 <0.25 -- <0.25 Appendixes 45

Appendix 4. Physical properties measured in groundwater samples from wells and a surface-water sample from irrigation ditch at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

[USGS, U.S. Geological Survey; °C, degrees Celsius; --, no data collected; mg/L, milligrams per liter; <, less than; µS/cm, microsiemens per centimeter at 25 degrees Celsius; NTRU, nephelometric turbidity ratio units]

USGS site- Well or Sample Air Dissolved pH, field Specific conduc- Water Turbidity identification site Date time temperature oxygen (standard tance, field temperature (NTRU) number identifier (24 hour) (°C) (mg/L) units) (µS/cm) (°C) 433615110440001 JH–1 06/08/2011 1200 -- 19.0 8.0 248 9.5 0.3 07/19/2011 1030 25.0 -- 7.9 260 9.8 0.7 11/01/2011 1100 -1.0 8.2 8.0 257 7.0 0.5 04/03/2012 1030 5.0 7.7 7.9 259 7.4 0.1 433604110443401 JH-1.5 06/11/2011 1030 -- 0.1 7.2 474 11.0 2.5 07/20/2011 1800 23.0 0.2 7.0 622 16.1 5.0 433604110443403 JH-1.5R 11/02/2011 1730 4.5 0.3 7.2 386 7.8 0.4 04/04/2012 1820 12 <0.1 7.2 350 8.3 0.3 433604110443403 JH-1.5D 06/10/2011 1150 -- 0.2 7.3 352 9.9 3.0 07/20/2011 1930 23.0 <0.1 7.4 396 9.2 1.5 11/03/2011 1300 6.5 0.1 7.3 368 9.6 4.0 04/05/2012 1020 5.5 <0.1 7.3 333 8.4 0.2 433551110443501 JH–2 06/08/2011 1710 -- 4.3 7.4 420 11.0 -- 07/19/2011 1530 26.0 4.7 7.3 419 12.0 1.2 11/01/2011 1510 1.5 3.3 7.6 321 7.5 0.6 04/03/2012 1530 13.5 4.1 7.5 321 8.6 0.2 433600110443701 JH-2.5 06/09/2011 1500 -- 0.2 7.5 401 10.8 0.4 07/21/2011 1100 22.0 0.3 7.3 436 10.7 1.3 11/03/2011 1430 8.5 0.1 7.5 347 10.4 0.3 04/04/2012 0950 10.0 1.0 7.3 332 7.9 0.5 433603110443501 JH–3 06/09/2011 1830 -- 0.1 7.3 408 9.7 0.1 07/20/2011 1100 23.0 0.2 7.1 488 15.5 1.0 11/02/2011 1350 3.5 0.1 7.2 395 7.7 0.3 04/04/2012 1250 16 <0.1 7.2 348 8.8 0.7 433603110443502 JH–3D 06/09/2011 2030 -- 0.1 7.3 342 9.0 0.9 07/20/2011 1300 23.0 0.1 7.3 379 15.7 0.8 11/02/2011 1510 4.5 0.2 7.4 335 10.5 5.0 04/04/2012 1450 16 0.1 7.5 307 903 0.7 433605110443801 JH-3.5 06/09/2011 1000 -- 0.3 7.7 307 9.4 2.0 07/20/2011 1430 25.0 0.2 7.3 571 11.3 2.5 11/02/2011 1110 2.5 0.1 7.2 388 7.7 0.5 433613110443501 JH–4 06/08/2011 1500 -- 8.2 8.0 253 10.8 0.6 07/19/2011 1300 28.0 8.0 7.9 258 11.4 0.7 11/01/2011 1330 4.5 8.0 8.0 247 8.2 0.3 04/03/2012 1300 11.0 7.5 7.8 252 7.9 0.5 433553110443601 Irrigation 06/08/2011 1840 -- 9.0 8.4 266 10.5 -- ditch 1Dissolved-oxygen concentration measured by laboratory was an average of 7.1 mg/L. This field measurement is presented in this table but was not used in analysis. 46 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Appendix 5. Analytical results for chemical oxygen demand, major ions, trace elements, nutrients, dissolved organic carbon, and stable isotopes in groundwater samples from wells and a surface-water sample from irrigation ditch at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012.

[USGS, U.S. Geological Survey; mg/L, milligrams per liter; --, not analyzed; <, less than symbol indicates the chemical was not detected and the value following the less than symbol is the laboratory reporting level; CaCO3, calcium carbonate; N, nitrogen; P, phosphorus; µg/L, micrograms per liter; H2S, dihydrogen sulfide; – – HS , hydrogen sulfide; 2S , sulfide;Bold value indicates constituent exceeded a U.S. Environmental Protection Agency Secondary Maximum Contaminant Level]

–

S, HS 2 (mg/L) 3 Date (µg/L) (µg/L) (µg/L) (µg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) number as P (mg/L) ), total, field (mg/L) – Time (24 hour) Time 2 Iron, dissolved as CaCO dissolved (mg/L) Sulfate, dissolved Sodium, dissolved Bicarbonate, field, Fluoride, dissolved Calcium, dissolved Nitrate plus nitrite, Bromide, dissolved Chloride, dissolved Potassium, dissolved level, dissolved, field Well or site identifier Well dissolved as N (mg/L) Manganese,dissolved Nitrite, dissolved as N Phosphorus, total as P high level, total (mg/L) Magnesium, dissolved Dissolved oxygen, low Dissolved solids (mg/L) Ferrous iron, total, field Silica, dissolved as SiO Sulfide (sum of H USGS site-identification Hardness, total, as CaCO Ammonia, dissolved as N nitrite plus ammonia and S Organic carbon, dissolved Chemical oxygen demand, Total nitrogen (nitrate plus Total Alkalinity, field, dissolved, Alkalinity, Orthophosphate, dissolved organic-N), unfiltered (mg/L) 433615110440001 JH–1 06/08/2011 1200 -- 156 120 35.2 7.83 1.93 7.71 120 146 0.013 3.47 0.43 18.6 9.75 ------<3.2 <0.16 ------JH–1 07/19/2011 1030 ------126 154 ------23.4 <0.16 ------JH–1 11/01/2011 1100 ------121 147 ------<3.2 <0.16 ------JH–1 04/03/2012 1030 <10 158 122 36.0 7.92 2.01 7.53 114 138 0.021 3.90 0.46 19.8 10.8 10.011 20.286 <0.001 0.019 0.016 0.24 <3.2 <0.16 0.49 ------433604110443401 JH–1.5 06/10/2011 1030 <10 267 254 79.9 13.1 2.25 8.22 263 321 0.025 5.28 0.34 19.8 1.99 0.017 20.02 <0.001 0.014 10.007 <0.05 223.9 967 0.69 <0.0050 <0.02 224 JH–1.5 07/20/2011 1800 <10 382 310 96.0 17.1 2.28 8.06 328 400 0.041 13.1 0.33 23.7 .24 <0.010 <0.02 <0.001 0.020 10.021 <0.05 2843 3,040 4.12 0.0075 0.89 153 433604110443403 JH–1.5R 11/02/2011 1730 ------206 251 ------2230 1,640 -- <0.0050 0.026 171 JH–1.5R 04/04/2012 1820 <10 245 173 54.8 8.72 1.88 7.50 153 186 0.022 4.16 0.45 20.9 9.43 10.039 <0.040 <0.001 0.008 0.009 <0.05 2153 1,120 0.51 <5.0 0.195 164 433604110443403 JH–1.5D 06/10/2011 1150 <10 224 171 52.9 9.54 2.02 8.20 178 217 0.016 4.88 0.39 19.2 5.64 <0.010 <0.02 <0.001 0.014 10.011 <0.05 2470 907 0.53 0.0050 0.53 76 JH–1.5D 07/20/2011 1930 <10 247 187 57.2 10.8 2.08 7.98 198 242 0.023 8.41 0.41 20.5 1.01 <0.010 <0.02 <0.001 0.013 10.017 <0.05 21,050 1,130 1.82 0.0545 1.05 294 JH–1.5D 11/03/2011 1300 -- 230 187 59.2 9.63 1.93 7.18 187 228 0.020 5.62 0.41 22.7 7.95 ------2931 1,450 -- <0.0050 1 213 JH–1.5D 04/05/2012 1020 <10 211 163 51.6 8.40 1.79 7.12 153 186 0.019 3.87 0.47 21.0 9.58 10.022 <0.040 <0.001 0.009 0.015 <0.05 2617 1,160 0.45 0.0070 0.69 355 433551110443501 JH–2 06/08/2011 1710 -- 258 223 67.8 13.1 2.32 8.35 215 262 0.017 4.67 0.33 19.3 8.05 <0.010 21.35 0.002 0.020 10.013 1.47 <3.2 <0.16 ------JH–2 07/19/2011 1530 -- 256 208 63.7 11.9 2.11 7.13 188 230 <0.010 6.18 0.33 18.9 11.2 <0.010 20.76 <0.001 0.021 10.011 0.78 <3.2 <0.16 ------JH–2 11/01/2011 1510 ------159 193 ------<3.2 <0.16 ------JH–2 04/03/2012 1530 <10 212 159 49.0 8.91 1.94 7.91 151 183 0.019 3.66 0.48 19.8 11.6 <0.010 20.197 <0.001 0.017 0.014 0.15 <3.2 10.32 0.42 ------433600110443701 JH–2.5 06/09/2011 1500 <10 229 205 63.9 11.0 2.10 8.24 204 249 0.018 4.61 0.38 19.1 6.59 <0.010 20.04 0.006 0.014 10.006 <0.05 <3.2 108 0.64 <0.0050 <0.02 192 JH–2.5 07/21/2011 1100 <10 256 213 66.2 11.7 2.15 7.79 218 266 0.032 9.98 0.37 19.8 4.53 <0.010 20.02 0.004 0.015 10.006 <0.05 27.2 61.7 10.8 <0.0050 0.075 246 JH–2.5 11/03/2011 1430 ------177 215 ------25.7 135 -- <0.0050 <0.02 240 JH–2.5 04/04/2012 0950 <10 257 162 51.3 8.29 1.94 7.39 155 189 0.018 3.77 0.46 19.4 11.1 0.079 <0.040 <0.001 0.027 0.039 0.21 247.1 8.92 0.83 <0.0050 0.06 0.06 433603110443501 JH–3 06/09/2011 1830 <10 240 213 65.6 11.8 2.01 8.14 222 270 0.015 4.82 0.35 21.2 3.52 <0.010 <0.02 <0.001 0.014 10.013 <0.05 2584 1,690 0.68 0.0055 0.6 142 JH–3 07/20/2011 1100 <10 292 245 75.7 13.7 2.24 8.17 248 302 0.029 9.33 0.35 22.4 0.16 0.014 <0.02 0.007 0.015 10.014 <0.05 2735 1,730 1.31 0.0240 0.78 237 JH–3 11/02/2011 1350 ------207 252 ------2515 1,530 -- <0.0050 0.55 248 JH–3 04/04/2012 1250 <10 210 167 52.6 8.71 1.85 7.03 161 196 0.023 3.89 0.46 20.2 9.50 0.294 <0.040 <0.001 0.055 0.111 0.92 2254 1,090 2.90 0.0090 0.28 162 433603110443502 JH–3D 06/09/2011 2030 <10 203 170 51.5 10.0 1.95 7.78 176 214 0.018 4.53 0.39 20.1 5.43 <0.010 <0.02 <0.001 0.012 10.012 <0.05 2592 1,030 0.72 0.0085 0.62 193 JH–3D 07/20/2011 1300 <10 218 180 54.5 10.8 2.08 7.95 195 237 0.012 6.56 0.38 21.0 1.87 0.012 <0.02 <0.001 0.015 10.012 <0.05 2572 1,060 10.71 0.0205 0.565 193 JH–3D 11/02/2011 1510 ------164 199 ------2648 898 -- 0.0120 0.76 237 JH–3D 04/04/2012 1450 <10 178 145 44.1 8.40 1.82 6.92 135 164 0.020 4.34 0.42 19.4 8.92 10.028 <0.040 <0.001 0.006 0.012 <0.05 2493 769 0.56 0.0230 0.6 513 433605110443801 JH–3.5 06/09/2011 1000 <10 189 157 47.6 9.29 2.09 7.16 162 197 0.018 3.73 0.39 17.4 8.14 <0.010 20.04 0.006 0.014 10.011 <0.05 27.1 21.3 0.53 <0.0050 <0.02 227 JH–3.5 07/21/2011 1430 <10 330 273 81.5 16.8 2.61 8.33 294 358 0.033 6.07 0.32 21.1 0.43 <0.010 <0.02 <0.001 0.015 10.007 <0.05 28.1 806 10.97 <0.0050 0.02 173 JH–3.5 11/02/2011 1110 ------210 256 ------2760 1,610 -- 0.0110 0.785 138 433613110443501 JH–4 06/08/2011 1500 -- 160 125 37.5 7.70 1.85 6.47 122 149 0.013 3.19 0.34 18.3 7.71 ------<3.2 0.21 ------JH–4 07/19/2011 1300 ------118 143 ------210.9 10.26 ------JH–4 11/01/2011 1330 ------120 145 ------23.7 <0.16 ------JH–4 04/03/2012 1300 <10 150 121 36.2 7.41 1.86 6.43 112 130 0.024 5.01 0.38 18.9 8.48 10.011 20.168 <0.001 0.017 0.014 0.14 24.2 10.18 0.36 ------433553110443601 Irrigation 06/08/2011 1840 20 169 123 35.8 8.09 1.33 10.5 105 126 <0.010 0.84 0.13 6.58 33.9 <0.010 <0.02 0.001 0.013 0.124 0.40 238.2 4.61 6.43 ------ditch Quality-control samples Quality-control samples 433605110443801 3JH–3.5 06/09/2011 1001 <10 177 156 47.4 9.24 2.09 7.15 160 195 0.016 3.72 0.39 17.2 8.14 <0.010 2.03 0.006 0.014 10.009 <0.05 15.2 22.4 0.56 ------1Quantified concentration in the environmental sample is less than five times the maximum concentration in a blank sample. 2Relative percent difference (RPD) between the groundwater sample and replicate sample is greater than 20 percent. 3Replicate. Appendixes 47

Appendix 5. Analytical results for chemical oxygen demand, major ions, trace elements, nutrients, dissolved organic carbon, and stable Appendix 5. Analytical results for chemical oxygen demand, major ions, trace elements, nutrients, dissolved organic carbon, and stable isotopes in groundwater samples from wells and a surface-water sample from irrigation ditch at Jackson Hole Airport, Jackson, Wyoming, isotopes in groundwater samples from wells and a surface-water sample from irrigation ditch at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012. water years 2011 and 2012.—Continued

[USGS, U.S. Geological Survey; mg/L, milligrams per liter; --, not analyzed; <, less than symbol indicates the chemical was not detected and the value following [USGS, U.S. Geological Survey; mg/L, milligrams per liter; --, not analyzed; <, less than symbol indicates the chemical was not detected and the value following the less than symbol is the laboratory reporting level; CaCO3, calcium carbonate; N, nitrogen; P, phosphorus; µg/L, micrograms per liter; H2S, dihydrogen sulfide; the less than symbol is the laboratory reporting level; CaCO3, calcium carbonate; N, nitrogen; P, phosphorus; µg/L, micrograms per liter; H2S, dihydrogen sulfide; – – – – HS , hydrogen sulfide; 2S , sulfide;Bold value indicates constituent exceeded a U.S. Environmental Protection Agency Secondary Maximum Contaminant Level] HS , hydrogen sulfide; 2S , sulfide;Bold value indicates constituent exceeded a U.S. Environmental Protection Agency Secondary Maximum Contaminant Level]

–

time 1150 1200 1030 1710 1500 1830 2030 1000 1001 1500 Sample (24 hour) date Sample 6/8/2011 6/8/2011 6/9/2011 6/9/2011 6/9/2011 6/9/2011 6/9/2011 6/8/2011 6/10/2011 6/10/2011 1 Well Well JH–1 JH–2 JH–3 JH–4 JH–3D JH–1.5 JH–2.5 JH–3.5 JH–3.5 JH–1.5D identifier Analyses for dissolved gases in groundwater samples from wells at the Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012. Analyses for dissolved gases in groundwater samples from wells at the Jackson Hole Airport, Jackson, Wyoming,

USGS number Replicate sample. 1 site-identification 433615110436001 433604110443401 433604110443402 433551110443501 433600110443701 433603110443501 433603110443502 433605110443801 433605110443801 433613110443501 Appendix 6. [USGS, U.S. Geological Survey] Appendixes 49

------1,3- <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) cis propene Dichloro-

------<1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 (µg/L) Bromo- methane value indicates that compound

Bold ------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) benzene 1,4-Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) propane 1,3-Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) propane 1,2-Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethane 1,2-Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethane 1,2-Dibromo- - , range of carbon compounds included in the analysis] Quality-control data 36

Groundwater-quality data Groundwater-quality ------C 10 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 pane (µg/L) 3-chloropro 1,2-Dibromo-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) chloro propane 1,2,3-Tri

Time 1150 1100 1100 1200 1030 1030 1030 1800 1820 1930 1020 1710 1530 1530 1500 0950 1830 1250 2030 1300 1450 1000 1430 1500 1300 1300 1840 1001 (24 hour) Date 06/08/2011 07/19/2011 06/10/2011 07/20/2011 06/10/2011 07/20/2011 06/08/2011 07/19/2011 06/09/2011 07/21/2011 06/09/2011 07/20/2011 06/09/2011 07/20/2011 06/09/2011 07/21/2011 06/08/2011 07/19/2011 06/08/2011 06/09/2011 04/03/2012 04/04/2012 04/05/2012 04/03/2012 04/04/2012 04/04/2012 04/04/2012 04/03/2012 ditch JH–1 JH–1 JH–1 JH–2 JH–2 JH–2 JH–3 JH–3 JH–3 JH–4 JH–4 JH–4 JH–3.5 JH–3D JH–3D JH–3D JH–1.5 JH–1.5 JH–2.5 JH–2.5 JH–2.5 JH–3.5 JH–3.5 2 JH–1.5R JH–1.5D JH–1.5D JH–1.5D identifier Irrigation Well or site Well Analytical results for volatile organic compounds, gasoline-range organics, and diesel-range organics in groundwater samples fr om wells a surface-water

USGS number site-identification 433551110443501 433615110440001 433604110443401 433604110443403 433604110443403 433600110443701 433603110443501 433603110443502 433605110443801 433613110443501 433553110443601 433605110443801 Appendix 7. water years 2011 and 2012. sample from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, compounds were unfiltered. USGS, U.S. Geological Survey; µg/L, micrograms per liter; --, not analyzed; <, less than symbol indicates compound was detected [All samples for analysis of volatile organic and the value following less than symbol is laboratory reporting level; E, level, but equal to or greater method detection limit; C was detected, but attributed to sample contamination; DRO, diesel-range organics; 50 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) chlorobenzene 1,2,3-Tri

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <1.0 (µg/L) propene 1,1-Dichloro- value indicates that compound

Bold

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethene 1,1-Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethane 1,1-Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethane chloro- 1,1,2-Tri

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) 1,1,2,2-Tetra- chloroethane

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethane chloro- 1,1,1-Tri

, range of carbon compounds included in the analysis] Quality-control data 36 Groundwater-quality data Groundwater-quality ------C 10 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) 1,1,1,2-Tetra chloroethane

------1,3- <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) propene trans Dichloro-

USGS number site-identification 433551110443501 433615110440001 433604110443401 433604110443403 433604110443403 433600110443701 433603110443501 433603110443502 433605110443801 433613110443501 433553110443601 433605110443801 Appendix 7. water years 2011 and 2012.—Continued sample from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, compounds were unfiltered. USGS, U.S. Geological Survey; µg/L, micrograms per liter; --, not analyzed; <, less than symbol indicates compound was detected [All samples for analysis of volatile organic and the value following less than symbol is laboratory reporting level; E, level, but equal to or greater method detection limit; C was detected, but attributed to sample contamination; DRO, diesel-range organics; Appendixes 51

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) 4-Iso- propyl- toluene

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <1.0 (µg/L) toluene 4-Chloro- value indicates that compound

Bold ------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) toluene 2-Chloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) propane 2,2-Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) benzene 1,3-Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) methylbenzene 1,3,5-Tri

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) benzene 1,2-Dichloro-

, range of carbon compounds included in the analysis] Quality-control data

- 36 Groundwater-quality data Groundwater-quality ------C 10 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) methylbenzene 1,2,4-Tri

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) chlorobenzene 1,2,4-Tri

USGS number site-identification 433551110443501 433615110440001 433604110443401 433604110443403 433604110443403 433600110443701 433603110443501 433603110443502 433605110443801 433613110443501 433553110443601 433605110443801 Appendix 7. water years 2011 and 2012.—Continued sample from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, compounds were unfiltered. USGS, U.S. Geological Survey; µg/L, micrograms per liter; --, not analyzed; <, less than symbol indicates compound was detected [All samples for analysis of volatile organic and the value following less than symbol is laboratory reporting level; E, level, but equal to or greater method detection limit; C was detected, but attributed to sample contamination; DRO, diesel-range organics; 52 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) chloromethane Dibromo-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethene cis-1,2- Dichloro- value indicates that compound

Bold ------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) Chloro- methane

------<1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 (µg/L) ethane Chloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) Chloro- benzene

------<1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 (µg/L) Bromo- methane dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) chloro- Bromo- methane

, range of carbon compounds included in the analysis] Quality-control data

36 Groundwater-quality data Groundwater-quality -C ------10 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) Bromo- benzene

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) E0.09 1 Benzene

USGS number site-identification 433551110443501 433615110440001 433604110443401 433604110443403 433604110443403 433600110443701 433603110443501 433603110443502 433605110443801 433613110443501 433553110443601 433605110443801 Appendix 7. water years 2011 and 2012.—Continued sample from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, compounds were unfiltered. USGS, U.S. Geological Survey; µg/L, micrograms per liter; --, not analyzed; <, less than symbol indicates compound was detected [All samples for analysis of volatile organic and the value following less than symbol is laboratory reporting level; E, level, but equal to or greater method detection limit; C was detected, but attributed to sample contamination; DRO, diesel-range organics; Appendixes 53

- tert ------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) butyl ether Methyl

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) chloride Methylene value indicates that compound

Bold ------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) benzene Isopropyl-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) butadiene Hexachloro-

------(µg/L) range <25 <25 <25 <25 <25 <25 <25 <25 <25 <25 <25 <25 E11 organics Gasoline-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) Ethyl- E0.11 benzene

36 -C 10 DRO <0.50 <0.51 <0.50 <0.52 <0.55 <0.52 <0.53 <0.54 <0.54 <0.51 <0.51 <0.53 <0.53 <0.52 <0.52 <0.51 <0.52 <0.49 <0.52 <0.52 <0.52 <0.53 <0.50 <0.52 <0.53 <0.50 <0.50 <0.53 C (mg/L)

, range of carbon compounds included in the analysis] Quality-control data 36 Groundwater-quality data Groundwater-quality -C ------10 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) difluoro- methane Dichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) methane Dibromo-

USGS number site-identification 433551110443501 433615110440001 433604110443401 433604110443403 433604110443403 433600110443701 433603110443501 433603110443502 433605110443801 433613110443501 433553110443601 433605110443801 Appendix 7. water years 2011 and 2012.—Continued sample from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, compounds were unfiltered. USGS, U.S. Geological Survey; µg/L, micrograms per liter; --, not analyzed; <, less than symbol indicates compound was detected [All samples for analysis of volatile organic and the value following less than symbol is laboratory reporting level; E, level, but equal to or greater method detection limit; C was detected, but attributed to sample contamination; DRO, diesel-range organics; 54 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

------Butyl- <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) benzene tert

------Butyl <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) tert ethyl ether value indicates that compound

Bold ------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) Styrene

------Butyl- <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) benzene sec

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) -Xylene o

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) -Propyl- benzene n

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 -Butyl- (µg/L) n benzene , range of carbon compounds included in the analysis] Quality-control data

36 Groundwater-quality data Groundwater-quality -C ------10 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 <1.0 (µg/L) Naph- thalene

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) -xylene p -Xylene and m

USGS number site-identification 433551110443501 433615110440001 433604110443401 433604110443403 433604110443403 433600110443701 433603110443501 433603110443502 433605110443801 433613110443501 433553110443601 433605110443801 Appendix 7. water years 2011 and 2012.—Continued sample from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, compounds were unfiltered. USGS, U.S. Geological Survey; µg/L, micrograms per liter; --, not analyzed; <, less than symbol indicates compound was detected [All samples for analysis of volatile organic and the value following less than symbol is laboratory reporting level; E, level, but equal to or greater method detection limit; C was detected, but attributed to sample contamination; DRO, diesel-range organics; Appendixes 55

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 E0.26 E0.20 total (µg/L) Xylene,

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 Vinyl Vinyl (µg/L) chloride

value indicates that compound ------<1.6 <1.6 <1.6 <1.6 <1.6 <1.6 <1.6 <1.6 <1.6 <1.6 <1.6 <1.6 <1.6 Bold (µg/L) Trihalo- methanes

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 form (µg/L) Chloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) fluoro methane Trichloro

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethene Trichloro-

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) Bromoform

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) ethene trans-1,2- Dichloro-

Quality-control data , range of carbon compounds included in the analysis] 36 ------Groundwater-quality data Groundwater-quality -C <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) 10 Toluene

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 tetra- (µg/L) Carbon chloride

------<0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 <0.50 (µg/L) Tetra- ethene chloro-

(24 Time 1150 1100 1100 1200 1030 1030 1030 1800 1820 1930 1020 1710 1530 1530 1500 0950 1830 1250 2030 1300 1450 1000 1430 1500 1300 1300 1840 1001 hour) Date 06/08/2011 07/19/2011 06/10/2011 07/20/2011 06/10/2011 07/20/2011 06/08/2011 07/19/2011 06/09/2011 07/21/2011 06/09/2011 07/20/2011 06/09/2011 07/20/2011 06/09/2011 07/21/2011 06/08/2011 07/19/2011 06/08/2011 06/09/2011 04/03/2012 04/04/2012 04/05/2012 04/03/2012 04/04/2012 04/04/2012 04/04/2012 04/03/2012

site ditch JH–1 JH–1 JH–1 JH–2 JH–2 JH–2 JH–3 JH–3 JH–3 JH–4 JH–4 JH–4 JH–3.5 JH–3D JH–3D JH–3D JH–1.5 JH–1.5 JH–2.5 JH–2.5 JH–2.5 JH–3.5 JH–3.5 Well or Well 2 JH–1.5R JH–1.5D JH–1.5D JH–1.5D identifier Irrigation Analytical results for volatile organic compounds, gasoline-range organics, and diesel-range organics in groundwater samples fr om wells a surface-water

USGS number Quantified concentration in the environmental sample is less than five times maximum a blank sample. Replicate sample. 1 2 site-identification 433551110443501 433615110440001 433604110443401 433604110443403 433604110443403 433600110443701 433603110443501 433603110443502 433605110443801 433613110443501 433553110443601 433605110443801 Appendix 7. water years 2011 and 2012.—Continued sample from irrigation ditch at the Jackson Hole Airport, Jackson, Wyoming, compounds were unfiltered. USGS, U.S. Geological Survey; µg/L, micrograms per liter; --, not analyzed; <, less than symbol indicates compound was detected [All samples for analysis of volatile organic and the value following less than symbol is laboratory reporting level; E, level, but equal to or greater method detection limit; C was detected, but attributed to sample contamination; DRO, diesel-range organics; 56 Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming

Appendix 8. Analytical results for triazoles in groundwater samples from wells and a surface-water sample from irrigation ditch at Jackson Hole Airport, Jackson, Wyoming, water years 2011 and 2012. [USGS, U.S. Geological Survey; µg/L, micrograms per liter; <, less than symbol indicates the chemical was not detected and the value following the less than symbol is the limit of detection; E, estimated concentration; Bold value indicates constituent was detected above the limit of quantitation; --, not applicable]

4-Methyl-1-H- 5-Methyl-1-H- USGS Well or site Benzotriazole Date Time Benzotriazole Benzotriazole site-identification number identifier (µg/L) (µg/L) (µg/L) 433615110440001 JH–1 06/08/2011 1200 <0.25 <0.35 <0.25 07/19/2011 1030 <0.25 <0.35 <0.25 11/01/2011 1100 <0.25 <0.35 <0.25 04/03/2012 1030 <0.25 <0.35 <0.25 433604110443401 JH-1.5 06/10/2011 1030 <0.25 2.1 2E0.33 07/20/2011 1800 <0.25 1.6 2E0.27 433604110443403 JH-1.5R 11/02/2011 1730 <0.25 13 2E0.68 04/04/2012 1820 <0.25 8.5 2E0.33 433604110443402 JH-1.5D 06/10/2011 1150 <0.25 2.2 2E0.33 07/20/2011 1930 <0.25 2.4 2E0.33 11/03/2011 1300 <0.25 9.8 2E0.77 04/05/2012 1020 <0.25 8.1 2E0.40 433551110443501 JH–2 06/08/2011 1710 <0.25 <0.35 <0.25 07/19/2011 1530 <0.25 <0.35 <0.25 11/01/2011 1510 <0.25 <0.35 <0.25 04/03/2012 1530 <0.25 <0.35 <0.25 433600110443701 JH-2.5 06/09/2011 1500 <0.25 4.3 2E0.43 07/21/2011 1100 <0.25 3.7 2E0.32 11/03/2011 1430 <0.25 7.8 2E0.72 04/04/2012 0950 <0.25 8.5 2E0.26 433603110443501 JH–3 06/09/2011 1830 <0.25 2.0 2E0.39 07/20/2011 1100 <0.25 1.8 2E0.41 11/02/2011 1350 <0.25 8.1 2E0.61 04/04/2012 1250 <0.25 8.7 2E0.52 433603110443502 JH–3D 06/09/2011 2030 <0.25 1.1 2E0.28 07/20/2011 1300 <0.25 1.1 2E0.26 11/02/2011 1510 <0.25 2.1 2E0.27 04/04/2012 1450 <0.25 3.0 2E0.31 433605110443801 JH-3.5 06/09/2011 1000 <0.25 <0.35 <0.25 07/21/2011 1430 <0.25 E0.37 <0.25 11/02/2011 1110 <0.25 1.2 2E0.28 April 2012 -- No sample No sample No sample 433613110443501 JH–4 06/08/2011 1500 <0.25 <0.35 <0.25 07/19/2011 1300 <0.25 <0.35 <0.25 11/01/2011 1330 <0.25 <0.35 <0.25 04/03/12 1300 <0.25 <0.35 <0.25 433553110443601 Irrigation ditch 06/08/2011 1840 <0.25 <0.35 <0.25 Quality assurance samples 433600110443501 1JH–2.5 06/09/2011 1300 <0.25 <0.35 <0.25 433605110443801 2JH–3.5 06/09/2011 1001 <0.25 <0.35 <0.25 433600110443501 1JH–2.5 07/21/2011 0900 <0.25 <0.35 <0.25 433605110443801 2JH–3.5 07/21/2011 1431 <0.25 <0.35 <0.25 433600110443501 2JH-2.5 11/03/2011 1431 <0.25 7.9 2E0.57 433604110443403 1JH-1.5R 04/04/2012 1630 <0.25 <0.35 <0.25 433604110443402 2JH-1.5D 04/05/2012 1021 <0.25 8.2 2E0.54 1Field blank. 2Replicate sample. Publishing support provided by: Rolla and Denver Publishing Service Centers

For more information concerning this publication, contact: Director, Wyoming Water Science Center U.S. Geological Survey 521 Progress Circle, Suite 6 Cheyenne, Wyoming 82007 (307) 778-2931

Or visit the Wyoming Water Science Center Web site at: http://wy.water.usgs.gov/ Wright—Hydrogeology and Water Quality in the Snake River Alluvial Aquifer at Jackson Hole Airport, Jackson, Wyoming—SIR 2013–5184 ISSN 2328-031X (print) ISSN 2328-0328 (online) http://dx.doi.org/10.3133/sir20135184